904-R-04-001b
Compendium of issues surrounding the levels of contaminants
contained in fish collected in tributaries leaving the
Oak Ridge Reservation (ORR) and associated risks from
exposure to those levels of contaminants : volume 2
Compiled by:
John R. Stockwell, MD, MPH
Captain, U.S. Public Health Service
prepared for:
U.S. Environmental Protection Agency
Region 4
2004
-------
Results from TV A Fish Tissue Studies on Fish Collected Autumn 1996
and Recommendations for Studies in 1997
By Don L Dycus
TVA Water Management
May 1997
Second Edition, August 1997, Revised Tables 1 and 2 and Appendices A and E
Introduction/Background
Because of significant interest by the fishing public and Valley states, TVA maintains an
annual program to examine contaminants in fish fillets from TVA reservoirs and their major
tributary streams. This systematic approach began in 1986 for streams and in 1987 for reservoirs
Prior fish tissue studies had been conducted on an "as needed" basis to address specific concerns.
This systematic approach is based on four types of studies, each with a different objective
yet working in concert with the others
• Screening Study: This is the most general study category. In these studies a composite
sample of the indicator species (channel catfish, if available) is collected from each site and
examined for a broad array of organics and metals suggested by EPA, 1995 (see Methods
section for citation). Also, largemouth bass are collected from each site and analyzed for
mercury only. Results from screening studies lead either to one of the more detailed study
categories below, if concentration of one or more analytes is high, or to a return to screening
on a 4-year rotational basis
• Targeted Screening Study: If Screening Studies find one or more analytes with moderately
elevated concentrations, then sampling is repeated at the same level the next year but only the
contaminant of concern is included in the analysis. Depending on results, a Targeted
Screening Study may continue at the same level of effort for a year or two to ensure that a
problem does not exist, lead to an Intensive Study if high levels of the contaminant are found;
or lead to the rotational screening system if concentrations are low.
• Intensive Study: In instances where concentrations in Screening or Targeted Screening
Studies are sufficiently high to pose potential human health concerns, the site or reservoir is
examined intensively to determine the species affected, the geographical distribution, and
year-to-year variation. Analysis of individual fish (generally 10 replicates) of important
species from several locations provide the data base for examinations. In selected cases,
replicate composite samples have been used in Intensive Studies. These studies are conducted
in close association with state agencies and usually result in some type of fish consumption
advisory being issued by the appropriate state agency. This assessment phase continues until
the contaminant concentration decreases to an insignificant level or until several years of
repeated study indicate concentrations are changing little from year-to year. In the former
case, the site or reservoir would return to the rotational system for screening In the latter
case, the reservoir/site would continued be examined but at a reduced effort in a Long-Term
Monitoring Study
-------
• Lone-Term Monitoring Study: The purpose of this study is to track the contaminant of
concern identified in an Intensive Study so that when concentrations decrease sufficiently a
follow-up Intensive Study can be conducted to provide sound evidence that the problem no
longer exists. Annual or rotational collections may be used depending on the particular
situation. Generally, composites of indicator species are analyzed for the analyte(s) of
concern.
This fish tissue monitoring program is now in what could be considered the maintenance
phase. Screening Studies have been conducted on all reservoirs and stream sites one or more
times. Most reservoirs and streams remain in the rotational screening category because elevated
contaminant levels have not observed. However, fish from several reservoirs and streams contain
high levels of selected contaminants (most commonly PCBs). Some of these problems were first
documented by this monitoring program and some were known to exist before this program
began. State agencies have issued advisories as appropriate (see Appendix A). These areas have
been examined in depth by conducting Intensive Studies and are now in the Long-Term
Monitoring phase.
The purpose of this document is to briefly provide results of samples collected in summer
and autumn 1996. Comparable documents are available for previous years from the address
provided below.
Methods
Details of TV A's collection, processing, and analysis procedures are described in the
report on 1993 fish tissue studies ~ "Tennessee Valley Reservoir and Stream Quality - 1993; Fish
Tissue Studies in the Tennessee Valley in 1993" by D.L. Williams and D.L. Dycus. The report
was published in July 1994 and is available from:
Water Management Library
Tennessee Valley Authority
1101 Market Street, CST 16B
Chattanooga, TN 37402-2810
(423) 751-7338 or FAX: (423) 751-7648
Prior to 1994 the only pesticides included in the analyses were organochlorine pesticides.
Beginning with that year, organophosphate and chlorophenoxy pesticides were analyzed as
recommended by the U.S. EPA in their "Guidance for Assessing Chemical Contaminant Data for
Use in Fish Advisories; Volume 1 Fish Sampling and Analysis" (EPA 823-R-93-007, September
1995).
-------
These include'
Organochlorine pesticide dicofol
Organophosphate pesticides, chlorpyrifos, diazinon, disulfoton, ethion, terbufos, and
carbophenothion
Chlorophenoxy pesticide' oxyfluorfen
The list was further expanded in 1996 for selected reservoirs to include dioxin
All laboratory analyses were performed by the TVA Environmental Chemistry Laboratory,
except analysis for dioxin, which was performed under contract by Wright State University in
Dayton, Ohio.
Summary of Results
Reservoirs and rivers included in fish tissue studies in 1996 are listed in Table 1 Results
from the various fish tissue studies conducted in 1996 are provided Tables 2-14 and Figures 1
and 2. Physical information such as length and weight for each fish is in Appendix B, Tables
B-l - B-4. Appendix C contains abbreviations for species and rivers used in tables and
appendices.
Table 2 - Summary Table, PCBs >0.5 |ig/g
Table 3 - Summary Table, Mercury >0.4 (ig/g
Reservoir Screening: Table 4 - Organics;
Table 5 - Metals;
Appendix Table B-l - Physical Information
Stream Screening: Table 6 - Organics
Table 7 - Metals
Appendix Table B-2 - Physical Information
Long-Term Monitoring: Table 8-Organics
Table 9 - Summary of PCB Concentrations in CHC
from Watts Bar, 1987- 1996
Table 10 - Data on Individual CHC from Fort Loudoun
Reservoir in 1996
Table 11 - Summary of PCB Concentrations in Fish
from Fort Loudoun 1985 - 1996
Appendix Table B-4 - Physical Information
Targeted Screening: Table 12 - Organics
Table 13 - Metals
Appendix Table B-4 - Physical Information
Dioxin Results: Table 14 - Summary
Appendix D - Detailed Results
-------
In general, 1996 results were similar to previous years Elevated levels of contaminants
were observed where they were known to exist and concentrations were low otherwise. The
most common contaminant of concern was PCBs Locations (regardless of study type) with PCB
concentrations >0.5 jig/g are listed in Table 2 Given the increasing interest in mercury, locations
(regardless of study type) with total mercury >0 40 ng/g are listed in Table 3
Dioxin results are summarized in Table 14 with details in Appendix D. As stated above,
1996 was the first year dioxin was included in TVA studies, but state studies have included dioxin
for several years. Concentrations of 2,3,7,8 TCDD ranged from 0.35 to 1.4 ppt (parts per
trillion), whereas TECs (toxicity equivalent concentrations) ranged from 0.87 to 5.0 ppt.
A detailed list of recommendations for fish tissue studies in 1997 is in Appendix E. (Note.
These recommendations were not final at the time this document was prepared.)
-------
Table 1 Alphabetical Listing of Reservoirs and Streams Included in Fish Tissue Studies in 1996.
Reservoir
State
Watershed
Advisory
(Yes/No)
Cause of
Advisory
Type Study
Screen Target Intensive Lone-T
Fish Species
Apalachia
NC
Hiwassee
No
X
CHC, LMJB
Bear Creek
AL
Pickwick/Wilson
No
X
CHC, LMB
Cedar
AL
Pickwick/Wilson
No
X
CHC, LMB
Chatuge
GA/NC
Hiwassee
No
X
CHC, LMB
Fontana
NC
Little Tenn.
No
X
CHC, LMB
Fort Loudoun
TN
Fort Hills Bar
Yes
PCBs
X
X
CHC, LMB
Guntersville
AL/TN
G'ville/Sequach
No
X
CHC, LMB
Hiwassee
NC
Hiwassee
No
X
CHC, LMB
L'Bear
AL
Pickwick/Wilson
No
X
CHC, LMB
Melton Hill
TN
Fort Hills Bar
Yes
PCBs
X
X
CHC, LMB
Ocoee No. 3
TN
Hiwassee
No
X
BGS, LMB, RES, YP
Ocoee No. 1
TN
Hiwassee
No
X
X
CHC, LMB
Pickwick
AL/TN/MS
PickwickAVilson
No
X
CHC, LMB
South Holston
TN
Holston
No
X
CHC, LMB
Watauga
TN
Holston
No
X
CHC, LMB
Watts Bar
TN
Fort Hills Bar
Yes
PCBs
X
X
CHC, LMB, STB
Wilson
AL
PickwickAVilson
No
X
CHC, LMB
Stream
Bear Creek
AL
PickwickAVilson
No
X
CHC, SPB
Buffalo River
TN
Duck
No
X
CHC, SMB
Clarks River
KY
Kentucky
No
X
CHC, LMB
Duck River
TN
Duck
No
X
CHC, SPB
French Broad R
TN
French Broad
No
X
CHC
Little Tenn. R
NC
Little Tennessee
No
X
CHC, SMB
Nolichucky R.
TN
French Broad
No
X
CHC, SMB
Pigeon River
TN
French Broad
Yes
Dioxin
X
CHC, SMB
Tuckasegee R.
NC
Little Tennessee
No
X
CHC, SMB
-------
Table 2. Highlights of Autumn 1996 Results from Areas with Advisories and/or "High"
(i.e., >0.5 |ig/g) PCB Concentrations with Comparisons to Results from Those
Areas in 1994 and 1995. All Samples Analyzed as 5-Fish Composites Unless
Otherwise Noted.
Location
Species
1994
1995
1996
Reservoirs
Guntersville Reservoir TRM 350
CHC
NS a
NS
<0.7
TRM 375
CHC
NS
NS
0.4
TRM 424
CHC
NS
NS
0.6
Melton Hill Reservoir
CRM 24
CHC
NS
NS
1.3
CRM 45
CHC
NS
NS
3.1
Parksville Reservoir
ORM 12
CHC
1.2
0.4
1 0
ORM 16
CHC
1.7
0.8
1.7
Watts Bar Reservoir
TRM 530/1
CHC
1.0
0.8
0.7
STB
NS
NS
1.2
TRM 560
CHC
1.0
1.2
2.1
STB
NS
NS
1.1
TRM 600
CHC
1.0
1.5
1.1
STB
NS
NS
1.3
CRM 22
CHC
NSb
NS b
0.7
STB
NS
NS
1.1
Ft. Loudoun Res
TRM 624
CHC
1.6°
1.5d
1.0'
Streams
Buffalo River
BuRM 18
CHC
0.4
0.4
0.5
Duck River
DRM 26
CHC
0.1
NS
0.6
a. NS - Not Sampled
b. Included in study by ORNL for DOE
c. Average of 9 channel catfish anaylzed individually
d. Average of 10 channel catfish analyzed individually
e. Average of 8 channel catfish analyzed individually
-------
Table 3. Highlights of 1996 Results from Reservoir and Stream Locations with "Elevated" (i e.,
>0.40 fig/g) Total Mercury Concentrations. Note Black Bass (Largemouth - LMB,
Smallmouth - SMB, and Spotted - SPB) Analyses Were Conducted on Five-fish
Composites Plus the Largest of the Five Individuals in the Composite Channel Catfish
(CHC) Were Analyzed as Five -fish 5 Composites
Comp./ Weight Mercury
Location Species Ind. (gm. if individual") CTotal. ua/a)
RESERVOIRS
Bear Creek - Bear Cr Mile 75
CHC
Comp
N/A
0.42
LMB
Ind
2065
1.1
Fontana - L' Tennessee R 62
CHC
Comp
N/A
0 40
LMB
Ind.
2800
0 46
L' Tennessee R. 81
LMB
Ind.
1110
0 40
Tuckasegee R 3
LMB
Ind
1014
0.59
Hiwassee - Hiwassee River 77
CHC
Comp
N/A
0.55
LMB
Comp
N/A
0.54
LMB
Ind.
1571
0.73
Hiwassee River 85
CHC
Comp
N/A
0.74
Pickwick - Tennessee R 230
LMB
Ind.
1020
0.66
South Holston - SFHRM 51
LMB
Comp.
N/A
0.43
LMB
Ind.
1944
0 72
SFHRM 62
LMB
Ind.
527
0.49
RIVERS
Bear Creek Mile 27
SPB
Comp.
N/A
0.56
SPB
Ind.
1757
1.0
Buffalo River Mile 18
SMB
Comp
N/A
0.61
SMB
Ind.
335
0.57
Clarks River Mile 10
LMB
Comp.
N/A
0.58
LMB
Ind
1099
0.62
L' Tennessee River Mile 95
SMB
Comp.
Comp.
0.43
SMB
Ind.
289
0 47
Tuckasegee River Mile 10
CHC
Comp.
N/A
0 45
SMB
Comp.
N/A
0.50
SMB
Ind.
943
0 78
Note. Additional mercury data are in the following tables, and weights for all fish are in the
appendices.
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Table 4. Concentrations (ug/g) of Selected Pesticides and PCBs in Composited Fish
Fillets Collected in 1996 For Reservoir Screening Studies.
For Calendar Year :1996
Collection Site
Spec.%LIPIDS MIREX
TOXAPH
HEPTA
ALDRIN
BENZ
DDT
DIELD
ENDO ENDRIN
CHLOR
PCB
DICOFOL
APPALACHIA
HIW 67.0
CHC
3.3
<0.008
<0.5
<0. 01
<0. 01
<0. 01
<0.010
<0.01
<0. 01
<0 . 01
<0 . 01
<0. 1
<0. 01
BEAR CREEK
BEC 75.0
CHC
3.6
<0.008
<0.5
<0. 01
<0.01
<0.01
<0.010
<0. 01
<0. 01
<0. 01
<0.01
0 . 1
<0.01
CEDAR CREEK
CEC 25.0
CHC
1.9
<0.008
<0.5
<0. 01
<0.01
<0.01
<0 .010
<0.01
<0. 01
<0.01
<0. 01
<0.1
<0 . 01
CHATUGE
HIW 122
CHC
4 . 5
<0.008
<0.5
<0. 01
<0.01
<0.01
<0.010
<0.01
<0. 01
<0 . 01
<0. 01
<0. 1
<0. 01
SHO 1.5
CHC
3.3
<0.008
<0.5
<0. 01
<0.01
<0. 01
<0.010
<0. 01
<0. 01
<0. 01
<0 .01
<0.1
<0. 01
FONTANA
LTE 62.0
CHC
6.6
<0.008
<0.5
<0. 01
<0.01
<0 . 01
<0.010
<0. 01
<0.01
<0 . 01
<0 . 01
0 . 2
<0 . 01
LTE 81.0
CHC
4 . 0
<0.008
<0.5
<0. 01
<0.01
<0.01
<0.010
<0.01
<0.01
<0.01
<0 . 01
0.1
<0 . 01
TUC 3.0
CHC
5.2
<0.008
<0.5
<0. 01
<0. 01
<0. 01
<0.010
<0. 01
<0. 01
<0. 01
<0. 01
<0. 1
<0. 01
GUNTERSVILLE
TEN 350
CHC
11.0
<0.008
<0.5
<0. 01
<0. 01
<0. 01
<0.010
<0.01
<0. 01
<0 . 01
<0. 01
0.7
<0. 01
TEN 375
CHC
10. 0
<0.008
<0.5
<0. 01
<0.01
<0. 01
<0.010
<0. 01
<0. 01
<0.01
<0 . 01
0.4
<0. 01
TEN 42 4
CHC
9.4
<0.008
<0.5
<0.01
<0.01
<0. 01
0. 03
<0.01
<0. 01
<0. 01
<0. 01
0 . 6
<0 . 01
HIWASSEE
HIW 77.0
CHC
5.4
<0.008
<0.5
<0. 01
<0.01
<0. 01
<0.010
<0. 01
<0.01
<0. 01
<0. 01
<0. 1
<0. 01
HIW 85.0
CHC
3.0
<0.008
<0.5
<0.01
<0. 01
<0.01
<0.010
<0. 01
<0.01
<0. 01
<0.01
0. 3
<0 . 01
LITTLE BEAR CREEK
LBC 12.0
CHC
4 . 0
<0.008
<0.5
<0.01
<0.01
<0.01
<0.010
<0. 01
<0. 01
<0. 01
<0. 01
<0. 1
<0 . 01
MELTON HILL
CLI 24.0
CHC
7 . 6
<0.008
<0.5
<0. 01
<0.01
<0.01
<0.010
<0.01
<0.01
<0. 01
<0 . 01
1. 3
<0. 01
CLI 45.0
CHC
7 . 7
<0.008
<0.5
<0. 01
<0.01
<0.01
<0.010
<0.01
<0.01
<0. 01
<0. 01
3 . 1
<0. 01
PARKSVILLE - OCOEE
N
OCO 12.0
CHC
2 . 7
<0.008
<0.5
<0. 01
<0.01
<0.01
<0.010
<0. 01
<0 . 01
<0 . 01
<0. 01
1 . 0
<0.01
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Tab| Concentrations (ug/g) of Selected Pe ides and PCBs in Composited Fish
Con Fillets Collected in 1996 For Reserv Screening Studies.
For Calendar Year :1996
Collection Site
Spec .%LIPIDS MI REX
TOXAPH
HEPTA
ALDRIN
BENZ
DDT
DIELD
ENDO
ENDRIN
CHLOR
PCB
DICOFOL
PICKWICK
BEC 8.0
CHC
4 . 3
<0.008
<0.5
<0. 01
<0. 01
<0.01
<0.010
<0. 01
<0. 01
<0.01
<0. 01
0.2
<0. 01
TEN 207
CHC
3.9
<0.008
<0.5
<0. 01
<0. 01
<0.01
<0.010
<0.01
<0.01
<0.01
<0.01
0.4
<0. 01
TEN 230
CHC
5.2
<0.008
<0.5
<0. 01
<0. 01
<0. 01
<0.010
<0. 01
<0. 01
<0. 01
<0.01
0.4
<0. 01
TEN 259
CHC
3 . 8
<0.008
<5.0
<0.01
<0. 01
<0.01
<0.010
<0.01
<0 . 01
<0.01
<0 . 01
0 . 3
<0.01
SOUTH HOLSTON
SFH 51.0
CHC
5.8
<0.008
<0.5
<0.01
<0. 01
<0.01
<0.010
<0.01
<0.01
<0. 01
<0. 01
<0. 1
<0. 01
SFH 62.0
CHC
5. 1
<0.008
<0.5
<0.01
<0. 01
<0 . 01
<0.010
<0 . 01
<0.01
<0.01
<0 . 01
0 . 4
<0 . 01
WATAUGA
WAT 37.0
CHC
7 . 0
<0.008
<0.5
<0. 01
<0. 01
<0.01
<0.010
<0.01
<0. 01
<0.01
<0.01
<0 . 1
<0 . 01
WAT 4 5.0
CHC
6.4
<0.008
<0.5
<0.01
<0. 01
<0 . 01
<0.010
<0 . 01
<0 . 01
<0 . 01
<0 . 01
<0 . 1
<0.01
WATTS BAR
CLI 22.0
CHC
9.8
<0.008
<0.5
<0. 01
<0. 01
<0.01
<0.010
<0.01
<0. 01
<0. 01
<0.01
0 . 7
<0 . 01
TEN 531
CHC
6.3
<0.008
<0.5
<0. 01
<0.01
<0.01
<0.010
<0.01
<0 . 01
<0 . 01
<0 . 01
0 . 7
<0 . 01
TEN 560
CHC
6. 1
<0.008
<0.5
<0. 01
<0. 01
<0.01
<0.010
<0.01
<0.01
<0. 01
<0. 01
2 . 1
<0 .01
TEN 600
CHC
3.3
<0.008
<0.5
<0. 01
<0. 01
<0.01
<0.010
<0.01
<0.01
<0. 01
<0. 01
1 . 1
<0. 01
WILSON
TEN 260
CHC
6.0
<0.008
<0.5
<0. 01
<0. 01
<0.01
<0.010
<0.01
<0.01
<0.01
<0 . 01
0 . 1
<0. 01
TEN 272
CHC
5.1
<0.008
<0.5
<0.01
<0. 01
<0.01
<0.010
<0.01
<0.01
<0 . 01
<0 . 01
0 . 4
<0 . 01
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Table A.
Cont.'
Collection Site
APPALACHIA
Concentrations (ug/g) of Selected Pesticides and PCBs in Composited Fish
Fillets Collected in 1996 For Reservoir Screening Studies.
For Calendar Year :1996
Spec. %LIPIDS DURSBAN DIAZINON DISULFOTON ETHION TERBUFOS CARBOPHENOTHION OXYFLUORFEN
HIW 67.0
BEAR CREEK
BEC 75.0
CEDAR CREEK
CEC 25.0
CHATUGE
HIW 122
SHO 1.5
FONTANA
LTE 62.0
LTE 81.0
TUC 3.0
GUNTERSVILLE
TEN 350
TEN 375
TEN 424
HIWASSEE
HIW 77.0
HIW 85.0
LITTLE BEAR CREEK
LBC 12.0
MELTON HILL
CLI 24.0
CLI 45.0
PARKSVILLE - OCOEE N
OCO 12.0 CHC
PICKWICK
BEC CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
3.3 <0.01
3.6 <0.01
1.9 <0.01
4 . 5
3.3
6.6
4 . 0
5.2
11.0
10. 0
9.4
5.4
3.0
7 . 6
7.7
<0.01
<0.01
<0. 01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0. 01
4.0 <0.01
<0.01
<0. 10
2.7 <0.01
4.3 <0.01
<0.01
<0.01
<0. 01
<0.01
<0.01
<0. 01
<0. 01
<0.01
<0. 01
<0. 01
<0.01
<0. 01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0. 01
<0.01
<0. 01
<0.01
<0.01
<0.01
<0.01
<0. 01
<0. 01
<0.01
<0.01
<0. 01
<0. 01
<0.01
<0.01
<0.01
<0. 01
<0.01
<0.01
<0. 01
<0.01
<0. 01
<0. 01
<0. 01
<0. 01
<0. 01
<0. 01
<0.01
<0.01
<0. 01
<0.01
<0. 01
<0. 01
<0. 01
<0.01
<0.01
<0.01
<0. 01
<0.01
<0. 01
<0. 01
<0.01
<0. 01
<0. 01
<0. 01
<0.01
<0.01
<0. 01
<0 . 01
<0.01
<0.01
<0. 01
<0.01
<0. 01
<0.01
<0.01
<0. 01
<0 . 01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0. 01
<0.01
<0 . 01
<0. 01
<0.01
<0.01
<0.01
<0.01
<0.01
<0. 01
<0.01
<0.01
<0. 01
<0.01
<0.01
<0. 01
<0.01
<0. 01
<0. 01
<0.01
<0. 01
<0. 01
<0.01
-------
Tat| Concentrations (ug/g) of Selected P< cides and PCBs in Composited Fish
Con— Fillets Collected in 1996 For Reser\w^~ Screening Studies.
For
Calendar Year
: 1996
Collection
Site
Spec.
%LIPIDS
DURSBAN
DIAZINON
DISULFOTON
ETHION
TERBUFOS
CARBOPHENOTHION
OXYFLUORFEN
TEN
207
CHC
3.9
<0.01
<0.01
<0. 01
<0.01
<0.01
<0.01
<0.01
TEN
230
CHC
5.2
<0 . 01
<0.01
<0.01
<0.01
<0.01
<0 . 01
<0.01
TEN 259
SOUTH HOLSTON
CHC
3.8
<0.01
<0.01
<0. 01
<0.01
<0. 01
<0. 01
<0 . 01
SFH
51.
, 0
CHC
5.8
<0. 01
<0. 01
<0. 01
<0. 01
<0. 01
<0.01
<0 . 01
SFH
WATAUGA
62.
, 0
CHC
5.1
<0.01
<0. 01
<0.01
<0.01
<0. 01
<0. 01
<0 . 01
WAT
37 .
, 0
CHC
7 . 0
<0.01
<0.01
<0.01
<0.01
<0. 01
<0 . 01
<0 . 01
WAT 4 5.
WATTS BAR
. 0
CHC
6.4
<0.01
<0. 01
<0. 01
<0. 01
<0.01
<0 . 01
<0.01
CLI
22 .
. 0
CHC
9.8
<0.01
<0.01
<0.01
<0.01
<0 . 01
<0 .01
<0. 01
TEN
531
CHC
6.3
<0.01
<0.01
<0.01
<0. 01
<0.01
<0 . 01
<0 . 01
TEN
560
CHC
6.1
<0. 01
<0.01
<0.01
<0.01
<0. 01
<0 . 01
<0 . 01
TEN
WILSON
600
CHC
3.3
<0.01
<0.01
<0. 01
<0. 01
<0. 01
<0. 01
<0 . 01
TEN
260
CHC
6.0
<0.01
<0.01
<0. 01
<0. 01
<0. 01
<0.01
<0 . 01
TEN
272
CHC
5.1
<0.01
<0.01
<0.01
<0. 01
<0. 01
<0.01
<0.01
-------
Table 5. Concentrations (ug/g) of Metals in Composited Fish Fillets Collected
in 1996 for Reservoir Screening Studies.
For Calendar Year :1996
Collection Site Species LABID As Cd Pb Hg Se
APPALACHIA
HIW 67.0 LMB 0.20
HIW 67.0 LMB 0.29*
HIW 67.0 CHC <0.10 < 0.05 < 0.02 0.39 <0.2
BEAR CREEK
BEC 75.0 CHC <0.10 < 0.05 < 0.02 0.42 <0.2
BEC 7 5.0 LMB 0.32
BEC 75.0 LMB 1.10*
CEDAR CREEK
CEC 25.0 CHC <0.10 < 0.05 < 0.02 0.22 <0.2
CEC 25.0 LMB 0.33
CEC 25.0 LMB 0.32*
CHATUGE
HIW 122 LMB 0.18
HIW 122 LMB 0.31*
HIW 122 CHC <0.10 < 0.05 < 0.02 0.17 <0.2
SHO 1.5 LMB 0.17
SHO 1.5 LMB 0.20*
SHO 1.5 CHC <0.10 < 0.05 < 0.02 0.27 0.3
FONTANA
LTE 62.0 CHC <0.10 < 0.05 < 0.02 0.40 <0.2
LTE 62.0 LMB 0-28
LTE 62.0 LMB 0.46*
LTE 81.0 CHC <0.10 < 0.05 0.26 0.34 <0.2
LTE 81.0 LMB °-39
LTE 81.0 LMB
0.40
*
TUC 3.0 CHC <0.10 < 0.05 < 0.02 0.16 <0.2
-------
Table 5 oncentrations (ug/g) of Metals in Compo d Fish Fillets Collected
Cont.' n 1996 for Reservoir Screening Studies.
For Calendar Year : 1996
Collection Site
TUC 3. 0
TUC 3.0
GUNTERSVILLE
HIWASSEE
HIW 77.0
HIW 77.0
HIW 77.0
HIW 85.0
HIW 85.0
HIW 8 5.0
LITTLE BEAR CREEK
LBC 12.0
LBC 12.0
LBC 12.0
MELTON HILL
CLI 24.0
CLI 2 4.0
CLI 24.0
Species LABID
LMB
LMB
As
Cd
Pb
LMB
LMB
CHC
CHC
LMB
LMB
CHC
LMB
LMB
LMB
LMB
CHC
<0.10
<0.10
< 0.05
< 0.05
0 . 43
< 0. 02
<0. 10
< 0.05
<0.02
Hg
0. 34
0.59*
Se
TEN
350
CHC
<0 . 10
<
o
o
<_n
< 0.02
<0.10
<0 . 2
TEN
350
LMB
<0. 10
TEN
350
LMB
0.14*
TEN
375
CHC
<0. 10
<
0. 05
0. 07
<0.10
<0 . 2
TEN
375
LMB
<0.10
TEN
375
LMB
<0.10*
TEN
424
CHC
<0. 10
<
0. 05
<0.02
<0.10
<0.2
TEN
424
LMB
0.15
TEN
424
LMB
0. 10*
<0.10 < 0. 05 < 0.02
0. 54
0. 73*
0. 55
0.74
0.25
0. 32*
0. 22
0.20
0.21*
<0. 10
0.18*
0.18
<0 . 2
<0.2
<0 . 2
<0 . 2
-------
Table b. Concentrations (ug/g) of Metals in Composited Fish Fillets Collected
Cont.' in 1996 for Reservoir Screening Studies.
For Calendar Year :1996
Collection Site
Species LABID
As
Cd
Pb
Hg
Se
CLI
45.0
CHC
<0.10
<
0. 05
<
0. 02
0.14
<0.2
CLI
45.0
LMB
0.16
CLI
45.0
LMB
0.12 *
PARKSVILLE - OCOEE N
OCO
12. 0
CHC
O
T—1
o
V
<
0.05
<
0. 02
0 . 12
0 . 4
OCO
12 . 0
LMB
0.23
OCO
12.0
LMB
0.34*
PICKWICK
BEC
8 . 0
CHC
A
O
h-1
O
<
0.05
<
0.02
0.28
<0.2
BEC
8 . 0
LMB
<0.10
<
0.05
<
0. 02
0. 19
0.2
BEC
8.0
LMB
0. 32*
TEN
207
CHC
<0.10
<
0.05
0. 03
<0.10
<0.2
TEN
207
LMB
A
O
h—1
O
<
0.05
<
0. 02
<0. 10
<0.2
TEN
207
LMB
0. 16*
TEN
230
CHC
<0.10
<
0. 05
<
0. 02
A
O
»-»
O
<0.2
TEN
230
LMB
<0.10
<
0. 05
<
0. 02
0.20
<0.2
TEN
230
LMB
0.66*
TEN
259
CHC
<0.10
<
0.05
<
0. 02
<0. 10
<0.2
TEN
259
LMB
0.10
<
0. 05
<
0. 02
<0.10
<0.2
TEN
259
LMB
<0.10*
SOUTH
HOLSTON
SFH
51.0
CHC
<0. 10
<
0 . 05
0 . 32
0 . 12
<0 . 2
SFH
51.0
LMB
0 .43
SFH
51. 0
LMB
0. 72*
SFH
62 . 0
CHC
<0 . 10
<
0 . 05
<
0.02
0.31
<0 . 2
SFH
62 . 0
LMB
0.28
SFH
62 . 0,
LMB
0.49*
-------
Table 5 incentrations (ug/g) of Metals in Compo d Fish Fillets Collected
C°nt. ' ^ 1996 for Reservoir Screening Studies.
For Calendar Year : 1996
Collection Site
Species LABID
As
Cd
Pb
Hg
Se
WATAUGA
WAT
37 . 0
CHC
A
O
o
<
0.05
0. 05
0. 35
<0 . 2
WAT
37 . 0
LMB
0.44
WAT
37.0
LMB
0.60 *
WAT
45.0
CHC
<0.10
<
0. 05
<
0.02
0.39
<0.2
WAT
45.0
LMB
0.64
WAT
45.0
LMB
0.58 *
WATTS
BAR
CLI
22.0
LMB
0. 12
CLI
22 . 0
LMB
0. 27 *
CLI
22.0
CHC
<0. 10
<
0.05
<
0. 02
A
O
t—-1
O
<0.2
TEN
531
LMB
0 . 12
TEN
531
LMB
0.20*
TEN
531
CHC
<0.10
<
0. 05
<
0 . 02
0. 16
<0.2
TEN
560
CHC
<0.10
<
0.05
<
0. 02
0. 17
<0 . 2
TEN
560
LMB
0. 16
TEN
560
LMB
0. 14*
TEN
600
LMB
0 . 13
TEN
600
LMB
0. 30*
TEN
600
CHC
<0.10
<
0. 05
0.78
0.40
<0.2
WILSON
TEN
260
CHC
<0. 10
<
0. 05
0. 18
O
1—1
o
V
<0.2
TEN
260
LMB
<0. 10
<
0. 05
<
0 . 02
0 . 11
<0 . 2
TEN
260
LMB
0.20*
TEN
272
CHC
<0. 10
<
0. 05
0. 04
<0 . 10
<0 . 2
TEN
272
LMB
<0.10
<
0. 05
<
0. 02
0. 13
<0.2
TEN
272
LMB
0.25*
* Identifies the largest LMB in the composite. This fish was analyzed individually for
-------
. Table 6. Concentrations (ug/g) of Selected Pesticides and PCBs in Composited Fish
Fillets Collected in 1996 For Stream Screening Studies.
For Calendar Year :1996
Collection Site
Spec .^LIPIDS MIREX
TOXAPH
HEPTA
ALDRIN
BENZ
DDT
DIELD
ENDO
ENDRIN
CHLOR
PCB
DICOFOL
BEC
27 . 0
CHC
2.3
<0.008
<0.5
<0. 01
<0.01
<0.01
<0.010
<0 . 01
<0.01
<0 . 01
<0 . 01
<0 . 1
<0 . 01
BUF
18 . 0
CHC
5.4
<0.008
<0.5
<0. 01
<0.01
<0.01
<0.010
<0 . 01
<0. 01
<0 . 01
<0 . 01
0 . 5
<0. 01
CLA
10.0
CHC
8.2
<0.008
<0.5
<0. 01
<0.01
<0.01
<0.010
<0 . 01
<0 . 01
<0 . 01
<0 . 01
<0 . 1
<0.01
DUC
26.0
CHC
7.3
<0.008
<0.5
<0. 01
<0. 01
<0. 01
0. 12
<0. 01
<0. 01
<0. 01
<0.01
0.6
<0. 01
FRE
77.0
CHC
2.7
<0.008
<0.5
<0. 01
<0.01
<0. 01
<0.010
<0. 01
<0. 01
<0. 01
<0.01
<0.1
<0. 01
LTE
95.0
CHC
2.4
<0.008
<0.5
<0.01
<0. 01
<0. 01
<0.010
<0.01
<0.01
<0. 01
<0.01
<0.1
<0. 01
NOL
10.0
CHC
9.2
<0.008
<0.5
<0.01
<0. 01
<0.01
<0.010
<0. 01
<0. 01
<0. 01
<0 .01
<0.1
<0. 01
PIG
7 . 0
CHC
2 . 8
<0.008
<0.5
<0.01
<0.01
<0.01
<0.010
<0. 01
<0. 01
<0. 01
<0.01
<0. 1
<0. 01
TUC
10.0
CHC
2.3
<0.008
<0.5
<0.01
<0.01
<0. 01
<0.010
<0. 01
<0.01
<0 . 01
<0.01
<0. 1
<0.01
-------
Tabj Concentrations (ug/g) of Selected :ides and PCBs in Composited Fish
Con Fillets Collected in 1996 For Stream reening Studies.
For Calendar Year : 1996
Collection Site
Spec.
%LIPIDS
DURSBAN
DIAZINON
DISULFOTON
ETHION
TERBUFOS
CARBOPHENOTHION
OXYFLUORFEN
BEC
27 . 0
CHC
2 . 3
<0. 01
<0.01
<0.01
<0.01
<0.01
<0 . 01
<0.01
BUF
18 . 0
CHC
5.4
<0.01
<0.01
<0. 01
<0.01
<0.01
<0.01
<0.01
CLA
10.0
CHC
8.2
<0.01
<0.01
<0. 01
<0.01
<0. 01
<0. 01
<0.01
DUC
26.0
CHC
7 . 3
<0. 01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
FRE
77 . 0
CHC
2 . 7
<0. 01
<0. 01
<0.01
<0.01
<0. 01
<0.01
<0.01
LTE
95.0
CHC
2 . 4
<0.01
<0.01
<0. 01
<0. 01
<0.01
<0.01
<0.01
NOL
10.0
CHC
9.2
<0 . 01
<0. 01
<0. 01
<0 . 01
<0.01
<0. 01
<0.01
PIG
7 . 0
CHC
2.8
<0.01
<0. 01
<0. 01
<0.01
<0. 01
<0.01
<0.01
TUC
10.0
CHC
2 . 3
<0.01
<0.01
<0. 01
<0.01
<0 . 01
<0 . 01
<0.01
-------
Table 7. Concentrations (ug/g) of Metals in Composited Fish Fillets Collected
in 1996 for Stream Screening Studies.
For Calendar Year : 1996
ollection Site
Species LABID
As
Cd
Pb
Hg
Se
BEC
27 . 0
CHC
<0. 10
<
0.05
0.15
0. 17
<0.2
BEC
27.0
SPB
0.56
BEC
27 . 0
SPB
1. 00*
BUF
18 . 0
CHC
<0 . 10
<
0.05
<
0. 02
0.14
<0 . 2
BUF
18 . 0
SMB
0 . 61
BUF
18 . 0
SMB
0 . 57*
CLA
10.0
CHC
o
I—1
O
V
<
0. 05
<
0. 02
0.27
0.2
CLA
10.0
LMB
0.58
CLA
10. 0
LMB
0. 62*
DUC
26.0
CHC
<0.10
<
0.05
<
0. 02
0. 12
<0.2
DUC
26.0
SPB
0. 32
DUC
26.0
SPB
0. 30 *
FRE
77. 0
CHC
<0.10
<
0. 05
0.25
0. 15
<0.2
LTE
95. 0
CHC
<0. 10
<
0.05
<
0. 02
0 .25
<0.2
LTE
95. 0
SMB
0.43
LTE
95. 0
SMB
0.47 *
NOL
10.0
CHC
0. 12
<
0. 05
0.23
0.13
<0.2
NOL
10.0
SMB
0. 17
NOL
10.0
SMB
0.24 *
PIG
7.0
CHC
<0. 10
<
0. 05
<
0. 02
o
rH
o
V
<0.2
PIG
7.0
SMB
0.20
PIG
7 . 0
SMB
0.29 *
TUC
10. 0
CHC
0.14
<
0. 05
0.45
<0.2
TUC
10.0
SMB
0.50
TUC
10. 0
SMB
0.78*
* Identifies the largest LMB, SPB, or SMB in a composite. This fish was also analyzed individually fojL Hg.
-------
Tabl
Concentrations (ug/g) of Selected Pe Ldes and PCBs in Composited Fish
Fillets Collected in 1996 For Long T< Studies.
For Calendar Year : 1996
Collection Site Spec.%LIPIDS MIREX TOXAPH HEPTA ALDRIN BENZ DDT DIELD ENDO ENDRIN CHLOR PCB
PARKSVILLE - OCOEE N
0C0 16.0 CHC 6.2 <0.010 <0.01 1.7
WATTS BAR
CLI 22.0 STB 12.0 0.11 <0.01 1.1
TEN 531 STB 10.0 0.14 <0.01 1.2
TEN 560 STB 11.0 0.11 <0.01 1.1
TEN 600 STB 9.8 0.11 <0.01 1.3
-------
Table 9. Summary of PCB Concentrations (|ig/g) in Channel Catfish Fillets from Watts Bar Reservoir, 1987 - 1996
Year
Location
Number
Weight
Mean
PCB
Mean PCB
of Fish
Range (gm)
Weight (gm)
Range
Cone.
1987
TRM 531
NS
-
-
-
-
TRM 560
6-Ind.
239 - 1786
1103
0 1 - 4.4
1 4
TRM 600*
10-Ind.
336 - 1330
757
0.4 - 3.1
1.5
1988
TRM 531
10-Ind.
494 -4210
1763
0.1 - 4.3
1.4
TRM 560
10-Ind.
411 -2765
1124
1.3 - 7.5
2.7
TRM 600
10-Ind.
829 - 2957
1289
0 8-44
2.4
1989
TRM 531 DOE
10-Ind.
320 - 1695
1033
0.2 - 1.5
0.8
TRM 560 UOE
9-Ind.
324 - 1015
544
0 1-05
0 3
TRM 600
7-lnd
425 - 3229
1437
0 4-42
1.8
1990
TRM 531
10-Ind.
322 - 2110
700
<01-27
0 6
TRM 560
10-Ind.
282 - 1521
838
<01-18
0 8
TRM 600
10-Ind.
208 - 3246
912
0.3 - 5.8
1 6
1991
TRM 531
10-Ind.
899 - 2323
1342
0 8 - 2.9
1 6
TRM 560
10-Ind.
1149 - 2812
1571
0 8-40
2.3
TRM 600
10-Ind.
466 - 1881
967
0.5 - 4.4
1 4
1992
TRM 53 I
10-Ind.
407 -4178
1514
0 3 - 5.6
1 7
TRM 560
10-Ind.
497 - 3563
1540
0 2 - 3.8
1 9
TRM 600
10-Ind.
464 - 2168
1018
0 4 - 6.2
1 9
1993
TRM 53 1 D0E
-
-
-
-
TRM 560
9-Ind.
500 - 2590
1086
0 4 - 2.3
1 2
TRM 600
10-Ind.
442 - 2884
931
0 1-36
1 1
1994
TRM 531
1-Comp.
511 - 2338
1213
N/A
1.0
TRM 560
1-Comp.
523 - 2394
1302
N/A
1 0
TRM 600
1-Comp.
496 -2348
958
N/A
I 0
1995
TRM 531
1-Comp.
437 - 2186
1260
N/A
0 8
TRM 560
1-Comp.
800 - 1021
907
N/A
1 2
TRM 600
1-Comp.
626 - 2047
1251
N/A
1 5
1996
TRM 531
1-Comp.
500 - 1836
1250
N/A
0 7
TRM 560
1-Comp.
1062 - 2877
2272
N/A
2 1
TRM 600
1-Comp.
714 - 3623
1809
N/A
1 1
• Some blue catfish were collected from this site rather than all channel catfish
-------
Table 10. Concentrations (ug/g) of Selected Pesticides and PCBs in Individual Fish Fillets Collected During Autumn 1996 from Fort
Loudoun Reservoir for Long-Term Monitoring
Collection Lgt. Wt. Lipid
Location Species Date (mm) (em) Sex (%) DDTr Chlord PCBs
TRM624 CHC 1 10/23/96 492 1222 Male 5.3 <0 01 <0.01 0 3
TRM624 CHC 2 10/23/96 608 2182 Male 3.4 0.11 <0.01 1.3
TRM624 CHC 3 10/23/96 426 662 Male 0.7 0.06 <0.01 1.0
TRM 624 CHC 4 10/24/96 406 524 Male 0.8 <0.01 <0.01 0 7
TRM624 CHC 5 10/25/96 597 2094 Female 4.4 0.11 <0 01 13
TRM624 CHC 6 10/25/96 480 1394 Male 3.1 0.06 <0.01 10
TRM 624 CHC 7 10/25/96 559 1608 Male 1.5 0.06 <0 01 14
TRM624 CHC 8 10/25/96 458 1060 Male 4.2 0.08 <0 01 0.9
-------
Table 11. Summary of PCB Concentrations in Channel Catfish, Carp, and White Bass Collected from Fort
Loudoun Reservoir for Period of Record, 1985 - 1996
Location
PCB Range
Mean
No.>2.0
# Fish
TRM
(ug/g)
fue/e)
fue/e)
Catfish
1985
628
0.2-2.8
1.4
2
10
1987
628
0.1-4.5
1.5
2
10
1988
628
0.2-4.4
1.2
1
10
1989
628
0.6-4.3
2.3
11
20
1990
628
0.3-1.9
1.0
0
10
1991
624
1.4-4.6
2.5
7
10
1992
624
0.1-4.2
1.8
3
9
1993
624
0.4-2.2
1.2
2
10
1994
624
0.6-3.1
1.6
3
9
1995
624
0.8-2.7
1.5
3
10
1996
624
0.3-1.4
1.0
0
8
Cart)
1992
651
0.2-0.9
0.6
0
10
White Bass
1987a
628
b
<0.1
a
5
640
b
<0.1
a
5
1992
651
0.3-1.2
0.5
0
10
a. Catfish were sampled from TRMs 624-629. White bass and carp were collected from TRM 651 in 1992
b. Five white bass were collected from TRMs 628 and 640 in 1987. Each set of five was analyzed as a composite sample
-------
Tah g.
Concentrations (ug/g) of Selected Pe Ldes and PCBs in Composited Fish
Fillets Collected in 1996 For Target greening Studies.
For Calendar Year : 1996
Collection Site Spec.%LIPIDS MI REX TOXAPH HEPTA ALDRIN BENZ DDT DIELD ENDO ENDRIN CHLOR PCB
OCOEE NO 3
0C0 30.0 LMB 0.5 <0.010 <0.01 <0.1
OCO 30.0 BGS 3.3 <0.010 <0.01 0.3
TUM 0.5 LMB 1.2 <0.010 <0.01 0.4
TUM 0.5 BGS 4.3 <0.010 <0.01 <0.1
TUM 0.5 RES 2.4 <0.010 <0.01 <0.1
TUM 0.5 YP 1.9 <0.010 <0.01 0.2
-------
Table 13. Concentrations (ug/g) of Metals in Composited Fish Fillets Collected
in 1996 for Targeted Screening Studies.
For Calendar Year : 1996
Collection Site Species LABID As Cd Pb Hg
OCOEE
NO 3
OCO
30. 0
LMB
0 . 14
<0 . 2
OCO
30 . 0
BGS
0. 12
<0 . 2
TUM
0.5
LMB
0. 17
0 . 6
TUM
0.5
BGS
0 . 16
1 . 0
TUM
0.5
RES
0.17
0 . 9
TUM
0.5
YP
0 . 15
0.4
-------
Table 14 Results of Analysis of Composited Channel Catfish Fillets from Selected TVA Reservoirs,
Sampled Autumn 1996 (2,3,7,8 TCDD and Total TEC in picograms per gram - ppt)
Location
River Mile
2,3,7,8 TCDD
Total TEC*
Pickwick Forebay
TRM 207
0.541
0.992
Trans. Zone
TRM 230
0.663
1.27
Inflow
TRM 259
0 445
0.868
Embayment
BCM 8
0.855
1 63
Wilson Forebay
TRM 260
1.30
2.52
Inflow
TRM 272
0 741
1.75
Guntersville Forebay
TRM 350
1.11
3.45
Tran. Zone
TRM 375
1.06
3.17
Inflow
TRM 424
1.41
3.43
Watts Bar Forebay
TRM 531
0.345
1.01
Trans. Zone
TRM 560
1.29
5.03
Inflow
TRM 600
1.26
4.31
Ft Loudoun Trans. Zone
TRM 624
0.802
2.00
Melton Hill Forebay
CRM 24
1.26
1.08
Trans. Zone
CRM 45
0.567
1.38
* TEC = Toxicity Equivalent Concentrations
-------
Figure 1. Average or Composite PCB Concentration (ug/g) in Channel Catfish Fillets
from Watts Bar Resevoir, 1987 - 1996
TRM 531
TRM 560
TRM 600
-------
Figure 2 Average PCB Concentrations (ng/g) in Channel Catfish from Fori Loudoun
Reservoir for Period of Record, 1985 - 1996
Fort Loudoun Reservoir
~
1985
H
1986
~
1987
U
1988
B
1989
~
1990
B
1991
O
1992
¦
1993
E
1994
~
1995
~
1996
TRM 624
-------
Appendix A
Fish Consumption Advisories
Alabama
Georgia
Tennessee
March 24, 1993
March 7, 1996
November 1996
-------
U5/15/96 15:08 PLRN utV - blS Ybl ('b^b
NEWS RELEASE department of public health
4.H Monroe Street, Mimitnmery. Al,ib.um. "fino-3017 • (334)
-------
!D-"k30 ri_riM -> did Oi io~>
-------
Wi/lb/SS rLHfN rco ucv -» o-3 fji
-------
1996
Guidelines for
Eating Fish
from Georgia Waters
Produced l>y:
Georgia Department of Natural Resources
Environmental Protection Division and
Wildlife Resources Division
205 Butler Street, S.E., Suite 1152
Atlanta, Georgia 30334
Georgia Lakes
Fish Consumption Guidelines
Lake Allatoona
Species
Less than 1 2
inches
12 - 16 inches
()\ cr 1 (> inches
(Jiem icn 1
C't nppie
No Reslnclions
(.';n |i
No KeMriUions
No IU si i k 1 ions
1 mc.il per weck
I't Ms
While Unss
1 HUM! |H I u
l'( 1U
1 .,ii):ciiioiilh Muss
No Kcslrn-iinns
1 me;il p'-r i\-\
V( IU
Lake llliickslicar
Species
Less (hnn 12
inches
12 - 1 Ci riu lies
Over 1 f> in< lies
( h o in i c :i 1
l.nigcnioulh Rns
No KcMnUmn.s
No Rt si r k tinn ¦>
Spoiled Sucker
No Resliiclions
No Resii iclions
Lake Blue Ridge
Species
Less than 12
inches
12 - IT) inches
Over 16 inches
Chemical
Wlnlc ["lass
1 me.il pci week
Mci cm \
Chniincl Catfisli
No Reductions
No RcMmcIioiis
II
-------
WNEWS
FOR MORE INFORMATION CONTACT:
Mary Locker: 615-532-0743
Paul Davis: 615-532-0625
FOR IMMEDIATE RELEASE WEDNESDAY, MARCH 24, ]9?3
NASHVILLE - The Department of Environment and Conservation's Division of Water Pollution
Control has announced that there will be no revisions at this time to the fishing advisories issued
in 1992.
"The department issues fish consumption advisories when testing indicates that levels of
toxic materials in fish tissue exceed those considered to be protective of human health, "said
Water Pollution Control Director Paul Davis. "Since the consumption of contaminated fish
tissue is an avoidable risk, the department issues advisories so that citizens can make informed
choices concerning their health.
"The results of 1992 studies of sites where advisories already existed or areas where
additional studies were needed have not justified revising or removing existing advisories or
issuing new ones at this time," Davis said. "However, the department will not hesitate to make
changes in the status of advisories during 1993 should new information become available."
Sites where samples were collected in 1992 include, but are not limited to. Watts Bar,
Chickamauga, Fort Loudoun, Douglas, Woods, Cheatham and Center Hill Reservoirs, as well as
the Mississippi, Wolf and Loosahatchie Rivers.
A list of the current advisories in Tennessee has been printed in the Tennessee Wildlife
Resources Agency's 1993 fishing regulations.
In order to assist citizens in their understanding of the stream posting process in
Tennessee, the Department of Environment and Conservation has prepared a free brochure
entitled "Tennessee Fishing Advisories." This publication explains the types of pollutants
impacting streams and the current locations of fishing advisories.
For more detailed information, or a copy of the brochure, contact the Department of
Environment and Conservation, Division of Water Pollution Control, 7th Floor, Life and
C*asnalrv Ann»y ifll fUnwl, • XT—i—rn_ t ~ . — .
Tennessee Department of Environment and Conservation
401 Churcr. Sdbs-.
Nasrtvihe T®nness®e 37?*;
-------
FISHING ADVISORY BACKGROUND INFORMATION
There are two principal reasons for posting streams in Tennessee. The
first is when bacterial contamination poses a water contact threat. Sources of
bacteria are most frequently from inadequately treated discharges from
municipal sewage systems, but can also be from livestock holding areas and
urban runoff. This type of advisory warns the public to avoid coining in
contact with these waters through activities such as swimming, wading,
fishing and skiing.
Streams are also posted when average levels of toxic materials in the
edible portion of fish pose an increased cancer risk (or other serious Illness)
to the genera] public. The department uses information and guidance from
the U.S. Food and Drug Administration and the Environmental Protection
Agency on the various contaminants found in fish.
There are two levels of fish consumption advisories used in Tennessee.
The mildest form is a "limit consumption advisory," sometimes referred to as a
precautionary advisory. Scientific studies have shown that developing fetuses
and children may be more susceptible to the harmful effects of toxic materials
than are adults. Thus a precautionary advisory warns that children,
pregnant women and nursing mothers should not eat the type fish that is
contaminated. All others are warned to limit their consumption of these fish.
The second level of advisory is a do-not-consume warning. At this
level, all persons are advised to avoid eating the type fish contaminated.
The department makes every attempt to get advisory information to the
public. A press release is issued whenever a stream or lake is posted. The
department also places warning signs at significant public points on
posted waters.
-------
CURRENT FISH TISSUE ADVISORIES (MARCH 1993)
STREAM COUNTY PORTION
Loosahatchw River Shelby Mil® D.0-20J
Wolf Kmv
Mississippi River
Boon* Reservoir
North Fork
Holston River
Fort Loudoun
Reservoir
Tellco Lake
Btgson River
Wans Bar
Reservoir
Me Ron Hill
Reservoir
East Fork of
Poplar Creek (mcL
Poplar Creek
emoayment)
Shelby
Shelby
Mite 0.0-18JB
MS kne to
mile 745
POLLUTANT
Chiordane
Chiordane
Chto rdane
McKellar Lake and Shelby
Nonsonnah Creek
mile 0.0 to Chiordane
Horn Lake Road
bndge (miU 1.6)
Sullivan, Entirety
Washington
Sullivan,
Hawkins
Loudon,
Knox,
Blount
Loudon
Cocke
Roane,
Meigs,
Rnea
Roane
Knox,
Anderson
Anderson,
Roane
Mile 0.0-5.2
TN/VA line
Entirely
(46 miles)
Entirety
(32.5 miles)
Mercury
PCBs
PCBs
N. Carolina line Dioxm
to Douglas Res.
Tennessee River PCBs
ponton
Clinch River
arm
Entirety
Mile 0.0 ¦
15.0
PCBs
PCBs
Mercury, metals,
org. chemicals
TYPE ADVISORY
Fish should not be consumed.
Fish should nol be consumed.
Fish should not be consumed.
CommercaJ fishing ban.
Fish should not be consumed.
PCBs. chiordane Precautionary advisory for carp and cattish.'
Fsh should not be consumed.
Commercial fishing lor cattish prohibited.
Catfish, largemoutn bass over two pounds,
and largemouth bass trom the Utile River
embay mem should not be consumed.
Catfish should not be consumed.
Fsh should not be consumed.
Catfish, striped bass, and hybrid striped bass-
white bass (Cherokee bass) should not be eaten.
Precautionary advisory* tor white bass, sauger,
carp, smaltmouth buffalo and largemouth bass.
Striped bass should not be consumed.
Precautionary advisory tor catfish and sauger.*
Catfish should not be consumed.
Fish should not be consumed.
Avoid contact wnh water.
Nicfcafack Reservoir Hamilton, Entirety
Marion
PCBs
Precautionary advisory for catfish*
Chattanooga Creek Hamilton GA line to mouth PCBs, chiordane
Woods Reservoir Franklin Entirety PCBs
Xhis list subject to revision.
Fish should not be consumed.
Catfish should not be consumed.
* Precautionary Advisory - Children, pregnant women, and nursing mothers should not consume the fsh tpy*»f named.
All other persons should bmit consumption of the named species tc 1.2 pounds per month.
-------
NEWS
Tennessee Department of Environment end Conservation
401 Church Street
Nashville. TennMMe 37243
For Immediate Release
March 7, 1996
For More Information Contact:
Melissa Miller, Public Information Office
615/532-0743 or
Paul E. Davis 615/532-0625
Greg Denton 615/532-0699
Nashville: Commissioner Don Dills of the Tennessee Department of Environment and
Conservation today announced a change to the fishing advisories for the state of Tennessee. The
body of water affected by today's change is the Pigeon River in Cocke County. The pollutant of
concern is dioxin.
Water Pollution Control Division Director Paul Davis said, "Fishing advisories arc issued when
levels of contaminants in fish pose an increased threat to the people who may eat them. Since
eating contaminated fish is an avoidable risk, we provide this information so that people can make
informed choices about their families' health."
"The change of advisory on the Pigeon River is a downgrading of the existing advisory made
possible by a trend of generally lower dioxin levels in fish in the last four years when compared to
levels documented in the 1980s," Davis said. 'The old advisory stated that no one should eat any
type of fish from the Pigeon River. Today's revision states that children, nursing mothers, and
pregnant women should avoid eating carp, catfish, and redbreast sunfish from the Pigeon. All other
persons should limit their consumption of Pigeon River carp, catfish, and redbreast sunfish to one
meal per month."
The Department now uses a risk-based procedure for issuing fishing advisories. An evaluation of
existing dioxin levels based on the new procedure indicate that certain Pigeon River fish continue to
pose a threat to atypical consumers of fish. The new dioxin advisory levels are 0.7 parts per trillion
for a precautionary advisory and 7.0 parts per trillion for a no consumption advisory. The average
levels of dioxin in Pigeon River catfish, carp, and redbreast sunfish continue to exceed the 0.7 level
for dioxin, but are well below 7 parts per trillion.
The Pigeon River originates in the Blue Ridge region of North Carolina and flows in a
northwesterly direction into Tennessee. During the 1980's, it was targeted for dioxin monitoring
during the U.S. Environmental Protection Agency's (EPA) National Dioxin Survey because of the
discharge of chlorine bleached pulp mill effluent near Canton, North Carolina. That and subsequent
analyses documented elevated levels of dioxin in fish.
The paper mill, Champion Paper Company, reached an agreement with EPA and the states of North
Carolina and Tennessee in 1990. As pan of that agreement, Champion invested over $300 million
in a pollution abatement and plant modernization project
(more)
-------
Since J 991, annual fish tissue monitoring has taken place in the Pigeon, primarily by the Champion
Paper Company as a compliance monitoring requirement of their NPDES permit and by the
Tennessee Wildlife Resources Agency (TWRA). Additional samples have been collected by
Carolina Power and Light and the Department of Environment and Conservation. Long-term goals
of this monitoring include providing data for the periodic reevaluation of the fishing advisory and
allowing the identification of trends, If any, in dioxin concentrations in fish over time.
Dioxin data collected during the period 1991 - 1995 are summarized below.
TYPE
DATA
AVERAGE
WEIGHTED •
E1S1L
RANGE
TEOfPPt)
AVERAGE TEO
Redbreast Sunfish
0.08-2.81
1.05
1.16
Common Carp
0.23 -14.55
4.14
4.57
Channel Catfish
0.50 - 9.04
3.14
3.54
Smallmouth Buffalo
0.09 - 1.06
0.57
0.52
Smallmouth Bass
0.11-0.80
0.38
0.24
Spotted Bass
0.19-0.76
0.49
0.53
'Average weighted according to the number of fish in composite samples.
Davis said, "The improvement in water quality in the Pigeon River is a result of the dedicated
efforts of many people. While the Pigeon is not yet as clean as it needs to be, and some dioxin
remains in fish, today's downgrading of the previous fishing advisory should be seen as a success
story in the making. We will continue to monitor the Pigeon River."
SUMMARY OF PIGEON RIVER ADVISORY CHANGES
SITE PREVIOUS ADVISORY NEW ADVISORY
Pigeon River (From North Carolina "Do not consume" advisory "Precautionary advisory*" for carp,
stale line to confluence with covering all types of fish. catfish, and redbreast sunfish.
French Broad River)
* Children, pregnant women, or nursing mothers should not eat these fish. Persons with
previous occupational exposure to the substance of concern should avoid eating any fish
from this site. All other should limit consumption of these fish to one meal per month.
Background information available upon request
-30-
-------
THE STATUS OF WATER QUALITY IN TENNESSEE
1996 305(b) REPORT
prepared by
Gregory M. Denton, Carole S. Freeman, and Katherine A. Larrieu
Water Supply and Ground Water Information submitted by
Robert Foster and Thomas Moss
NOVEMBER 1996
Tennessee Department of Environment and Conservation
Division of Water Pollution Control
401 Church Street
L&C Annex, 6th Floor
Nashville, Tennessee 37243-1534
615-532-0625
ii
-------
CURRENT FISH TISSUE ADVISORIES
(November, 1996. This list subject to revision.)
STREAM
COUNTY
PORTION
POLLUTANT
COMMENTS
Loosahatchie River
Shelby
Mile 0 0 - 20 9
Chlordane
Fish should not be consumed
Wolf River
Shelby
Mile 0 0- 189
Chlordane
Fish should not be consumed
Mississippi River
Shelby
MS line to mile 745
Chlordane
Fish should not be consumed Commercial fishing prohibited by TWRA
McKellar Lake &
Nonconnah Creek
Shelby
Mile 0 0 to 1.8
Chlordane
Fish should not be consumed Advisory ends at 1 lorn Uike Road budge
North Fork Holston River
Sullivan, 1 lawkins
Mile 0.0-6.2
Mercury
Fish should not be consumed. Advisory goes to TN/VA line
liast Fork of Poplar Creek
incl Poplar Ck embayment
Anderson, Roane
Mile 0.0-15 0
Mercury, PCBs
Fish should not be consumed Avoid contact with water also
Chattanooga Creek
1 Iainilton
Mouth to GA line
PCBs, chlordane
Fish should not be consumed Avoid contact with water also
Woods Reservoir
Franklin
Entirety
PCBs
Catfish should not be consumed
Fort Loudoun Reservoir
Loudon, Knox,
Blount
Entirety (46 miles)
PCBs
Commercial fishing for catfish prohibited by 1WRA Catfish,
largemouth bass over two pounds, or any largemoutli bass from the Little
River embayment should not be consiuned
Tellico Lake
Loudon
Entirety
PCBs
Catfish should not be consumed
Melton I Iill Reservoir
Knox, Anderson
Entirety
PCBs
Catfish should no! be consumed
Watts Bar Reservoir
Roane, Meigs,
Rhea, Loudon
Tennessee River portion
PCBs
Catfish, striped bass, & hybrid striped buss-white bass should not be
consiuned Precautionary advisory* for wlutebass, Sanger, carp, smallmoiith
bufialo and largeinoutli bass
Watts liar Reservoir
Roane, Anderson
Clinch River arm
PCBs
Striped bass should not be consumed Piecautionaiy advisory lor cattish and
sauger *
Boone Reservoir
Sullivan,
Washington
Entirety
PCBs, chlordane
Precautionary advisory for carp and catfish *
Nickajack Reservoir
I Iainilton, Marion
Entirety
PCBs
Precautionary advisory for cattish *
Pigeon River
Cocke
N.C line to Douglas Res
Dioxin
Precautionary advisory for carp, catfish, und redbreast simfisli *
~Precautionary Advisory - Children, pregnant women, and nursing mothers should not consume the fish species named All other persons should limit
consumption of the named species to one meal per month.
-------
Appendix B
Physical Information on All Fish Collected
for Fish Tissue Studies in 1996
Note: The following tables contain collection date, length, weight, and sex
for each fish included in these studies. Separate tables are provided for each
type of study. For each study, data are grouped by reservoir, river mile and
species. Individuals of the same species which were composited for analysis are
listed in successive order. In Reservoir and Stream Screening Studies
(Tables B-l and B-2, respectively), the largest individual from each
largemouth, smallmouth, or spotted bass composite was also analyzed
separately for mercury. These fish (i.e., those analyzed separately) are
identified in these tables by an asterisk (*). Data for each of these fish are
identical to the data for one of the entries above it because it is the same fish.
-------
Table B-l. Specific Information About Each Fish Collected During 1996 for
Reservoir Screening Fish Tissue Study
For Calendar Year :1996
:
ction Site
Date
Species
Length(mm)
Weight(g)
Sex
HIW 67 . 0
11/05/96
CHC
582
1664
Female
HIW
67 . 0
11/05/96
CHC
550
1290
Female
HIW
67 . 0
11/20/96
CHC
583
1647
Male
HIW
67 . 0
11/20/96
CHC
605
1749
Male
HIW
67.0
11/20/96
CHC
511
885
Male
HIW
67 . 0
11/05/96
LMB
552
1170
Female
HIW
67 . 0
11/05/96
LMB
334
528
Male
HIW
67.0
11/05/96
LMB
317
402
Female
HIW
67 . 0
11/05/96
LMB
421
991
Female
HIW
67. 0
11/05/96
LMB
382
698
Female
HIW
67 . 0
11/05/96
LMB*
552
1170
Female
BEAR
BEC
CREEK
75.0
09/23/96
CHC
515
1375
Female
BEC
75.0
09/23/96
CHC
570
2240
Male
BEC
75.0
09/23/96
CHC
541
1510
Male
BEC
75.0
09/23/96
LMB
370
705
Female
75.0
09/23/96
LMB
418
1145
Male
;
75. 0
09/23/96
LMB
340
535
Female
BEC
75.0
09/23/96
LMB
411
1030
Male
BEC
75. 0
09/23/96
LMB
488
2065
Male
BEC
75. 0
09/23/96
LMB*
488
2065
Male
CEDAR
CEC
CREEK
25. 0
09/25/96
CHC
555
2025
Female
CEC
25.0
09/25/96
CHC
379
430
Male
CEC
25.0
09/25/96
CHC
400
510
Female
CEC
25. 0
10/30/96
CHC
480
805
Male
CEC
25.0
10/30/96
CHC
391
435
Male
CEC
25. 0
09/25/96
LMB
306
380
Male
CEC
25.0
09/25/96
LMB
463
1490
Male
CEC
25 . 0
10/29/96
LMB
315
375
Female
CEC
25. 0
10/29/96
LMB
468
1490
Female
CEC
25. 0
10/29/96
LMB
443
1145
Female
CEC
25.0
10/29/96
LMB*
468
1490
Female
CHATUGE
_utW 122
10/01/96
LMB
466
1132
Female
122
10/01/96
LMB
362
616
Female
m W
122
10/01/96
LMB
442
1263
Male
LABID
Page 1
-------
Table B-l. Specific Information About Each Fish Collected During 1996 for
Cont.' . . , .
Reservoir Screening Fish Tissue Study
For Calendar Year : 1996
Collection Site
Date
Species
Length(mm)
Weight (g)
Sex
HIW
122
10/01/96
LMB
381
661
Male
HIW
122
10/01/96
LMB
321
437
Male
HIW
122
10/01/96
LMB*
442
1263
Male
HIW
122
10/01/96
CHC
464
817
Female
HIW
122
10/01/96
CHC
531
1427
Male
HIW
122
10/01/96
CHC
392
455
Male
HIW
122
11/05/96
CHC
459
743
Female
HIW
122
11/05/96
CHC
553
1561
Male
SHO
1.5
11/04/96
CHC
538
1520
Male
SHO
1.5
11/04/96
CHC
672
3109
Male
SHO
1. 5
11/04/96
CHC
546
1429
Male
SHO
1.5
11/04/96
CHC
488
910
Female
SHO
1.5
11/04/96
CHC
581
1690
Male
SHO
1.5
10/02/96
LMB
380
744
Male
SHO
1.5
10/02/96
LMB
313
383
Male
SHO
1.5
10/02/96
LMB
322
389
Male
SHO
1.5
10/02/96
LMB
372
540
Male
SHO
1.5
10/02/96
LMB
325
422
Male
SHO
1.5
10/02/96
LMB*
380
744
Male
FONTANA
LTE
62 . 0
10/03/96
CHC
440
690
Male
LTE
62 . 0
10/24/96
CHC
485
950
Female
LTE
62. 0
10/24/96
CHC
542
1121
Male
LTE
62.0
10/24/96
CHC
512
1040
Female
LTE
62 . 0
10/24/96
CHC
530
1369
Female
LTE
62.0
10/03/96
LMB
306
375
Male
LTE
62.0
10/03/96
LMB
386
842
Female
LTE
62.0
10/03/96
LMB
435
1183
Female
LTE
62.0
10/03/96
LMB
370
677
Female
LTE
62.0
10/03/96
LMB
322
474
Male
LTE
62.0
10/03/96
LMB*
435
1183
Female
LTE
81.0
10/01/96
LMB
356
587
Female
LTE
81.0
10/01/96
LMB
426
1068
Male
LTE
81.0
10/01/96
LMB
312
389
Female
LTE
81. 0
10/01/96
LMB
397
745
Female
LTE
81.0
10/01/96
LMB
432
1110
Female
LTE
81.0
10/01/96
LMB*
432
1110
Female
LABID
Page 2
-------
Table
B-l. Specific
Information About
Each Fish
Collected
During 1
Cont.
Reservoir
Screening
Fish Tissue Study
For Calendar Year :
1996
ction Site
Date
Species
Length (ram)
Weight(g)
Sex
LTE
81.0
10/24/96
CHC
495
1232
Male
LTE
81. 0
10/01/96
CHC
438
556
Male
LTE
81.0
10/24/96
CHC
441
891
Female
LTE
81. 0
10/24/96
CHC
535
1515
Male
LTE
81. 0
10/24/96
CHC
535
1243
Male
TUC
3.0
10/02/96
CHC
407
543
Male
TUC
3.0
10/02/96
CHC
496
949
Male
TUC
3.0
10/02/96
CHC
411
549
Female
TUC
3.0
10/02/96
CHC
414
570
Female
TUC
3.0
10/02/96
CHC
374
368
Female
TUC
3.0
10/02/96
LMB
363
731
Female
TUC
3 . 0
10/02/96
LMB
407
1014
Male
TUC
3.0
10/02/96
LMB
422
963
Female
TUC
3.0
10/02/96
LMB
364
610
Male
TUC
3.0
10/02/96
LMB
388
975
Male
TUC
3 . 0
10/02/96
LMB*
407
1014
Male
GUNTERSVILLE
350
10/09/96
CHC
562
2505
Female
350
10/09/96
CHC
560
1985
Female
TEN
350
10/09/96
CHC
461
1190
Male
TEN
350
10/09/96
CHC
525
1720
Male
TEN
350
10/09/96
CHC
435
825
Male
TEN
350
10/09/96
LMB
410
935
Female
TEN
350
10/09/96
LMB
366
730
Female
TEN
350
10/09/96
LMB
382
790
Female
TEN
350
10/09/96
LMB
431
1090
Female
TEN
350
10/09/96
LMB
365
715
Male
TEN
350
10/09/96
LMB *
431
1090
Female
TEN
375
10/08/96
LMB
360
770
Female
TEN
375
10/08/96
LMB
347
640
Female
TEN
375
10/20/96
LMB
370
1000
Female
TEN
375
10/20/96
LMB
385
955
Female
TEN
375
10/20/96
LMB
383
985
Male
TEN
375
10/20/96
LMB*
370
1000
Female
TEN
375
10/08/96
CHC
610
2850
Female
F
375
10/08/96
CHC
576
2060
Female
375
10/08/96
CHC
607
2280
Female
LABID
Page 3
-------
Table B-l.
Cont.'
Reservoir
Screening
Fish
For
Tissue Study
Calendar Year :
1996
Collection Site
Date
Species Length(mm)
Weight(g)
Sex
TEN
375
10/08/96
CHC
590
2520
Female
TEN
424
10/07/96
CHC
497
1450
Male
TEN
424
10/07/96
CHC
464
1070
Female
TEN
424
10/07/96
CHC
502
1340
Male
TEN
424
10/07/96
CHC
391
605
Female
TEN
424
10/07/96
CHC
390
685
Female
TEN
424
11/15/96
LMB
383
700
Female
TEN
424
11/15/96
LMB
418
865
Female
TEN
424
11/15/96
LMB
387
716
Female
TEN
424
11/15/96
LMB
420
924
Female
TEN
424
11/15/96
LMB
429
1292
Female
TEN
424
11/15/96
LMB *
429
1292
Female
HIWASSEE
HIW 77.0
10/04/96
LMB
356
791
Male
HIW
77. 0
10/04/96
LMB
362
716
Female
HIW
77. 0
10/04/96
LMB
456
1345
Female
HIW
77. 0
10/04/96
LMB
364
645
Male
HIW
77.0
10/04/96
LMB
466
1571
Female
HIW
77. 0
10/04/96
LMB *
466
1571
Female
HIW
77. 0
10/04/96
CHC
419
571
Male
HIW
77.0
11/20/96
CHC
459
817
Female
HIW
77. 0
11/20/96
CHC
572
1938
Female
HIW
77. 0
11/20/96
CHC
598
2382
Male
HIW
77. 0
11/20/96
CHC
492
898
Male
HIW
85. 0
10/03/96
CHC
538
1526
Female
HIW
85.0
10/03/96
CHC
398
475
Female
HIW
85. 0
10/03/96
CHC
521
1132
Female
HIW
85.0
10/03/96
CHC
411
562
Female
HIW
85. 0
10/03/96
LMB
362
782
Male
HIW
85. 0
10/03/96
LMB
362
753
Male
HIW
85. 0
10/03/96
LMB
386
854
Female
HIW
85.0
10/03/96
LMB
362
692
Female
HIW
85. 0
10/03/96
LMB
362
772
Male
HIW
85. 0
10/03/96
LMB *
386
854
Fema1e
LITTLE
LBC
BEAR CREEK
12. 0
09/24/96
LMB
334
515
Male
LBC
12.0
09/24/96
LMB
329
460
Female
During 1996 for
LABID
Page 4
-------
Table B-l. Specific Information About Each Fish Collected During 1996 for
Cont.' . . ^
Reservoir Screening Fish Tissue Study
For Calendar Year :
; 1996
~
tion Site
Date
Species
Length(mm)
Weight(g)
Sex
LBC
12 . 0
09/24/96
LMB
307
415
Male
LBC
12. 0
09/24/96
LMB
265
280
Female
LBC
12.0
09/24/96
LMB
364
550
Female
LBC
12 . 0
09/24/96
LMB*
364
550
Female
LBC
12. 0
09/24/96
CHC
502
1095
Female
LBC
12.0
09/24/96
CHC
548
1405
Male
LBC
12.0
09/24/96
CHC
504
1190
Male
LBC
12.0
09/24/96
CHC
508
1090
Male
LBC
12 . 0
09/24/96
CHC
460
905
Male
MELTON
HILL
CLI
24 . 0
10/15/96
LMB
470
1638
Female
CLI
24 . 0
10/15/96
LMB
339
486
Female
CLI
24 . 0
10/15/96
LMB
334
510
Female
CLI
24 . 0
10/15/96
LMB
403
868
Female
CLI
24 . 0
10/15/96
LMB
342
504
Female
CLI
Z4 . 0
10/15/96
LMB*
470
1638
Female
CLI
24 . 0
10/16/96
CHC
427
632
Male
24 . 0
12/04/96
CHC
566
1743
Female
24 . 0
12/04/96
CHC
575
1873
Male
CLI
24 . 0
12/04/96
CHC
520
1539
Female
CLI
24.0
12/04/96
CHC
586
1789
Female
CLI
45.0
10/17/96
CHC
646
3003
Female
CLI
45.0
10/17/96
CHC
698
5096
Male
CLI
45.0
10/17/96
CHC
647
3456
Male
CLI
45.0
10/17/96
CHC
716
4820
Male
CLI
45.0
10/17/96
CHC
635
3244
Female
CLI
45.0
10/16/96
LMB
388
690
Male
CLI
45.0
10/16/96
LMB
306
238
Female
CLI
45.0
10/16/96
LMB
392
806
Female
CLI
45.0
10/16/96
LMB
351
518
Female
CLI
45.0
10/16/96
LMB
315
368
Male
CLI
45.0
10/16/96
LMB*
392
806
Female
PARKSVILLE - OCOEE N
OCO
12 . 0
10/17/96
LMB
312
370
Female
OCO
12 . 0
10/17/96
LMB
346
576
Female
)
12. 0
10/17/96
LMB
353
655
Female
)
12 . 0
10/17/96
LMB
494
1963
Female
Page 5
-------
Table B-l. Specific Information About Each Fish Collected During 1996 for
Cont,
Reservoir Screening Fish Tissue Study
For Calendar Year :1996
Collection Site
Date
Species
Length(mm)
Weight(g)
Sex
OCO
12 . 0
10/17/96
LMB
531
2024
Female
OCO
12 . 0
10/17/96
LMB *
531
2024
Female
OCO
12.0
10/10/96
CHC
472
835
Male
OCO
12.0
10/17/96
CHC
447
746
Male
OCO
12.0
10/17/96
CHC
426
574
Female
OCO
12 . 0
10/17/96
CHC
424
607
Female
OCO
12.0
10/17/96
CHC
447
654
Male
LABID
PICKWICK
BEC
8.0
10/22/96
LMB
366
600
Female
BEC
8.0
10/22/96
LMB
347
625
Female
BEC
8 . 0
10/22/96
LMB
324
370
Female
BEC
8 . 0
10/22/96
LMB
315
400
Male
BEC
8 . 0
10/22/96
LMB
310
340
Female
BEC
8.0
10/22/96
LMB *
347
625
Female
BEC
8.0
10/22/96
CHC
519
1160
Male
BEC
8.0
10/22/96
CHC
492
1065
Female
BEC
8.0
10/22/96
CHC
461
790
Female
BEC
8.0
10/22/96
CHC
469
770
Male
BEC
8.0
10/22/96
CHC
392
490
Male
TEN
207
10/21/96
CHC
408
730
Male
TEN
207
10/21/96
CHC
418
695
Male
TEN
207
10/21/96
CHC
397
525
Male
TEN
207
10/22/96
CHC
430
735
Female
TEN
207
10/22/96
CHC
576
1800
Male
TEN
207
10/21/96
LMB
427
1125
Female
TEN
207
10/21/96
LMB
375
780
Female
TEN
207
10/21/96
LMB
309
440
Female
TEN
207
10/21/96
LMB
282
320
Male
TEN
207
10/21/96
LMB*
427
1125
Female
TEN
.230
10/23/96
LMB
446
1020
Male
TEN
230
10/23/96
LMB
380
820
Male
TEN
230
10/23/96
LMB
282
315
Male
TEN
230
10/23/96
LMB*
446
1020
Male
TEN
230
10/23/96
CHC
422
650
Female
TEN
230
10/23/96
CHC
446
895
Female
TEN
230
10/23/96
CHC
410
705
Female
TEN
230
10/23/96
CHC
403
625
Male
Page 6
-------
Table
B-l. Specific
Information About Each
Fish
Collected
During 1
Cont.
Reservoir
Screening
Fish Tissue
Study-
For Calendar
Year :
1996
ction Site
Date
Species Length(mm)
Weight(g)
Sex
TEN
230
10/23/96
CHC
446
750
Female
TEN
259
10/24/96
CHC
374
385
Male
TEN
259
10/24/96
CHC
377
425
Male
TEN
259
10/24/96
CHC
408
465
Female
TEN
259
10/24/96
CHC
501
1100
Male
TEN
259
10/24/96
CHC
392
585
Male
TEN
259
10/24/96
LMB
358
695
Female
TEN
259
10/24/96
LMB
305
445
Female
TEN
259
10/24/96
LMB
318
495
Male
TEN
259
10/24/96
LMB
405
309
Male
TEN
259
10/24/96
LMB*
358
695
Female
SOUTH
HOLSTON
SFH
51. 0
10/29/96
CHC
459
664
Female
SFH
51.0
10/29/96
CHC
511
1124
Female
SFH
51.0
11/13/96
CHC
507
950
Male
SFH
51. 0
10/29/96
LMB
512
1944
Female
SFH
51. 0
10/29/96
LMB
451
1376
Female
f
51. 0
10/29/96
LMB
463
1580
Female
I
51. 0
10/29/96
LMB
445
1536
Female
SFH
51.0
11/13/96
LMB
395
1044
Female
SFH
51. 0
10/29/96
LMB*
512
1944
Female
SFH
62.0
10/29/96
LMB
474
1414
Female
SFH
62.0
10/29/96
LMB
527
2300
Female
SFH
62.0
10/29/96
LMB
435
1168
Female
SFH
62.0
10/29/96
LMB
439
1182
Female
SFH
62 . 0
10/29/96
LMB
327
510
Female
SFH
62.0
10/29/96
LMB*
527
2300
Female
SFH
62.0
10/30/96
CHC
661
2823
Female
SFH
62.0
10/30/96
CHC
612
2274
Male
SFH
62.0
10/30/96
CHC
491
1041
Male
SFH
62. 0
10/30/96
CHC
445
703
Female
WATAUGA
WAT 37.0
WAT 37.0
WAT 37.0
r 37.0
r 37 . 0
11/07/96
11/07/96
10/31/96
10/31/96
10/31/96
CHC
CHC
LMB
LMB
LMB
502
540
421
479
495
1000
1139
1063
1596
2163
Male
Male
Female
Female
Female
LABID
Page 7
-------
Table B-l. Specific Information About Each Fish Collected During 1996 for
Cont* Reservoir Screening Fish Tissue Study
For Calendar Year :1996
LABID
Collection Site
Date
Species
Length(mm)
Weight(g)
Sex
WAT
37 . 0
10/31/96
LMB
366
690
Female
WAT
•37. 0
10/31/96
LMB
456
1865
Female
WAT
37 . 0
10/31/96
LMB *
495
2163
Female
WAT
45. 0
10/31/96
LMB
531
2655
Female
WAT
45.0
10/31/96
LMB
438
1451
Female
WAT
45. 0
10/31/96
LMB
386
811
Female
WAT
45.0
10/31/96
LMB
406
974
Female
WAT
45.0
10/31/96
LMB
480
1467
Female
WAT
45.0
10/31/96
LMB*
531
2655
Female
WAT
45.0
10/31/96
CHC
727
4001
Female
WAT
45. 0
10/31/96
CHC
385
440
Female
WAT
45. 0
11/26/96
CHC
454
939
Female
WATTS BAR
CLI 22.0
CLI
CLI
CLI
CLI
CLI
CLI
CLI
TEN
TEN
TEN
TEN
TEN
TEN
TEN
TEN
TEN
TEN
TEN
TEN
TEN
TEN
TEN
TEN
22.0
22.0
22. 0
22.0
22.0
22 . 0
22 . 0
531
531
531
531
531
531
531
531
531
531
560
560
560
560
560
560
10/07/96
10/07/96
10/07/96
10/07/96
10/07/96
10/07/96
10/07/96
10/07/96
10/08/96
10/08/96
10/08/96
10/08/96
10/08/96
10/08/96
10/09/96
10/09/96
10/09/96
10/17/96
10/17/96
10/17/96
10/17/96
10/17/96
10/23/96
10/09/96
CHC
CHC
LMB
LMB
LMB
LMB
LMB
LMB *
LMB
LMB
LMB
LMB
LMB *
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
LMB
584
506
460
363
314
348
315
460
457
341
452
314
457
394
547
446
554
523
529
595
491
619
618
417
2334
1008
1418
732
376
614
444
1418
1442
536
1402
438
1442
500
1835
917
1836
1164
1122
2529
1062
2622
2877
1028
Female
Male
Female
Female
Female
Female
Female
Female
Female
Female
Female
Female
Female
Male
Female
Male
Female
Female
Male
Male
Female
Male
Female
Female
Page
8
-------
Table B-l. Specific Information About Each Fish Collected During 1996 for
Cont.'
Reservoir Screening Fish Tissue Study
For Calendar Year :1996
:tion Site
Date
Species
Length(mm)
Weight(g)
Sex
TfcN
560
10/09/96
LMB
430
1081
Female
TEN
560
10/09/96
LMB
409
901
Female
TEN
560
10/09/96
LMB
415
1241
Female
TEN
560
10/09/96
LMB
303
413
Female
TEN
560
10/09/96
LMB*
415
1241
Female
TEN
600
10/10/96
LMB
451
1396
Female
TEN
600
10/10/96
LMB
3540
748
Female
TEN
600
10/10/96
LMB
378
858
Female
TEN
600
10/10/96
LMB
345
564
Female
TEN
600
10/10/96
LMB
324
440
Female
TEN
600
10/10/96
LMB*
451
1396
Female
TEN
600
10/10/96
CHC
435
714
Male
TEN
600
10/23/96
CHC
603
1963
Female
TEN
600
10/23/96
CHC
676
3623
Male
TEN
600
10/23/96
CHC
463
938
Male
LABID
WILSON
TEN
TEN
TEN
TEN
TEN
TEN
TEN
TEN
TEN
TEN
TEN
TEN
TEN
TEN
TEN
TEN
TEN
260
260
260
260
260
260
260
260
260
260
272
272
272
272
272
272
272
272
272
10/16/96
10/16/96
10/16/96
10/16/96
10/16/96
10/16/96
10/16/96
10/16/96
10/16/96
10/16/96
10/17/96
10/17/96
10/17/96
10/17/96
10/17/96
10/17/96
10/17/96
10/17/96
10/17/96
CHC
CHC
CHC
CHC
CHC
LMB
LMB
LMB
LMB
LMB*
LMB
LMB
LMB
LMB*
CHC
CHC
CHC
CHC
CHC
560
595
495
480
429
440
386
384
365
440
390
347
305
390
430
465
4 02
490
445
1535
2075
1085
970
620
1295
750
860
745
1295
810
595
335
810
720
1090
510
1080
825
Male
Female
Female
Male
Female
Female
Female
Female
Female
Female
Male
Male
Male
Male
Fema1e
Female
Female
Male
Female
Page
9
-------
Table B-2. Specific Information About Each Fish Collected During 1996 for
Stream Screening Fish Tissue Study
For Calendar Year : 1996
btion Site
Date
Species
Length(mm)
Weight(g)
Sex
BLL
27. 0
07/24/96
SPB
492
1757
Female
BEC
27 . 0
07/24/96
SPB
434
1088
Female
BEC
27 . 0
07/24/96
SPB
454
1423
Female
BEC
27 . 0
07/24/96
SPB *
492
1757
Female
BEC
27 . 0
07/24/96
CHC
414
631
Female
BEC
27.0
07/24/96
CHC
459
827
Male
BEC
27.0
07/24/96
CHC
359
371
Female
BEC
27.0
07/24/96
CHC
361
379
Female
BUF
18 . 0
05/31/96
CHC
504
1260
Female
BUF
18.0
05/31/96
CHC
392
463
Male
BUF
18.0
05/31/96
CHC
484
1093
Female
BUF
18 . 0
05/31/96
CHC
467
943
Female
BUF
18.0
05/31/96
CHC
446
891
Female
BUF
18.0
05/31/96
SMB
262
178
Female
BUF
18.0
05/31/96
SMB
300
335
Female
BUF
18.0
05/31/96
SMB
276
254
Female -
BUF
18.0
05/13/96
SMB *
300
335
Female
10.0
07/10/96
CHC
392
648
Female
10.0
07/10/96
CHC
504
1229
Male
CLA
10.0
07/10/96
LMB
339
703
Female
CLA
10.0
07/10/96
LMB
414
1099
Female
CLA
10.0
07/10/96
LMB
387
956
Fema1e
CLA
10.0
07/10/96
LMB*
414
1099
Female
DUC
26.0
06/05/96
SPB
264
212
Fema1e
DUC
26.0
06/05/96
SPB
268
212
Female
DUC
26.0
06/05/96
SPB
249
183
Fema1e
DUC
26.0
06/05/96
SPB
330
568
Female
DUC
26.0
06/05/96
SPB*
330
568
Female
DUC
26.0
06/05/96
CHC
661
3543
Male
DUC
26.0
06/05/96
CHC
515
1564
Female
DUC
26.0
06/05/96
CHC
514
1389
Female
DUC
26.0
06/05/96
CHC
465
945
Male
DUC
26.0
06/05/96
CHC
468
880
Female
FRE
77.0
09/24/96
CHC
430
663
Female
ERE
77.0
09/24/96
CHC
425
608
Female
77.0
09/24/96
CHC
468
930
Male
r nt
77.0
09/24/96
CHC
379
409
Male
Page 1
-------
Table B-2. Specific Information About Each Fish Collected During 1996 for
Cont.'
Stream Screening Fish Tissue Study
For Calendar Year : 1996
Collection Site
Date
Species
Length(mm)
Weight(g)
Sex
FRE
77 . 0
09/24/96
CHC
450
750
Male
LTE
95. 0
07/22/96
SMB
255
208
Female
LTE
95. 0
07/22/96
SMB
231
135
Female
LTE
95. 0
09/03/96
SMB
303
289
Female
LTE
95. 0
09/03/96
SMB*
303
289
Female
LTE
95. 0
07/22/96
CHC
405
497
Male
LTE
95. 0
07/25/96
CHC
403
563
Female
LTE
95. 0
09/03/96
CHC
379
410
Male
NOL
10. 0
07/15/96
CHC
401
574
Female
NOL
10. o'
07/15/96
CHC
604
2269
Female
NOL
10. 0
07/15/96
CHC
546
1618
Female
NOL
10.0
09/05/96
CHC
556
2018
Female
NOL
10.0
09/05/96
CHC
523
1467
Male
NOL
10.0
07/15/96
SMB
365
669
Female
NOL
10. 0
09/05/96
SMB
330
537
Female
NOL
10.0
09/05/96
SMB
223
171
Female
NOL
10.0
09/05/96
SMB*
365
669
Female
PIG
7.0
07/11/96
SMB
378
686
Female
PIG
7.0
07/11/96
SMB
327
361
Female
PIG
7.0
07/11/96
SMB
455
1370
Female
PIG
7.0
07/11/96
SMB
333
445
Female
PIG
7.0
07/11/96
SMB
320
481
Female
PIG
7.0
07/17/96
SMB*
455
1370
Female
PIG
7.0
07/11/96
CHC
383
545
Male
PIG
7.0
07/11/96
CHC
429
759
Female
PIG
7.0
07/11/96
CHC
430
665
Female
PIG
7.0
07/11/96
CHC
365
502
Male
PIG
7.0
07/11/96
CHC
310
272
Female
TUC
10.0
08/20/96
CHC
370
430
Female
TUC
10. 0
08/20/96
CHC
391
580
Male
TUC
10.0
09/19/96
CHC
381
464
Male
TUC
10.0
09/19/96
CHC
376
448
Female
TUC
10.0
08/20/96
SMB
446
943
Female
TUC
10. 0
09/19/96
SMB
290
332
Female
TUC
10. 0
09/19/96
SMB
244
331
Female
TUC
10.0
09/19/96
SMB
326
496
Female
TUC
10.0
09/19/96
SMB
271
264
Female
Page 2
-------
Table B-2. Specific Information About Each Fish Collected During 1996 for
Cont" Stream Screening Fish Tissue Study
For Calendar Year : 1996
=tion Site Date Species Length(mm) Weight(g) Sex LABID
"TOC 10.0 08/20/96 SMB* 446 943 Female
Page 3
-------
Table B-3. Specific Information About Each Fish
Term Fish Tissue Study
For Calendar Year
ction Site Date Species Length(mm)
jtakkdVILLE - OCOEE N
OCO 16.0 10/10/96 CHC 501
OCO 16.0 10/10/96 CHC 560
OCO 16.0 10/10/96 CHC 488
OCO 16.0 10/10/96 CHC 496
OCO 16.0 10/10/96 CHC 518
WATTS BAR
Collected During 1996 for Long
1996
Weight(g) Sex LABID
1027
1270
1005
1013
1215
Sex
Male
Male
Female
Female
Male
CLI
22 . 0
10/07/96
STB
742
4980
Female
CLI
22.0
10/07/96
STB
720
4506
Female
CLI
22 . 0
10/07/96
STB
909
9710
Female
CLI
22 . 0
10/07/96
STB
660
3288
Female
CLI
22.0
12/03/96
STB
717
4335
Female
TEN
531
10/17/96
STB
726
4223
Female
TEN
531
10/17/96
STB
642
3706
Male
TEN
531
10/17/96
STB
708
4946
Female
TEN
531
10/17/96
STB
643
3477
Male
TEN
531
10/17/96
STB
683
5318
Female
560
10/17/96
STB
585
3158
Male
560
10/23/96
STB
651
4252
Male
TEN
560
10/23/96
STB
520
2151
Female
TEN
560
10/23/96
STB
741
4633
Male
TEN
560
10/23/96
STB
631
3948
Female
TEN
600
10/10/96
STB
686
4539
Female
TEN
600
10/10/96
STB
888
8809
Female
TEN
600
10/22/96
STB
737
3994
Female
TEN
600
10/22/96
STB
619
3147
Male
TEN
600
10/22/96
STB
733
5834
Female
Page 1
-------
Table B-4. Specific Information About Each Fish Collected During 1996 for
Targeted Fish Tissue Study
For Calendar Year :1996
ction Site Date Species Length(mm) Weight(g) Sex LABID
OCUKfc NO 3
oco
o
o
CO
04/29/96
BGS
239
331
Male
oco
30.0
04/29/96
BGS
204
220
Male
oco
30. 0
04/29/96
BGS
201
154
Female
oco
30.0
04/29/96
BGS
188
153
Male
oco
30. 0
04/29/96
BGS
197
132
Female
oco
30. 0
04/29/96
LMB
344
583
Female
oco
30.0
04/29/96
LMB
261
201
Male
TUM
0.5
04/29/96
LMB
375
712
Male
TUM
0.5
04/29/96
BGS
228
263
Female
TUM
0.5
04/29/96
BGS
219
256
Female
TUM
0.5
04/29/96
BGS
214
240
Male
TUM
0.5
04/29/96
BGS
215
237
Male
TUM
0.5
04/29/96
BGS
215
228
Female
TUM
0.5
04/29/96
RES
278
443
Female
TUM
0.5
04/29/96
RES
263
412
Female
TUM
0.5
04/29/96
RES
265
379
Male
f
0.5
04/29/96
RES
258
370
Female
F
\
0.5
04/29/96
RES
265
362
Female
TUM
0.5
04/29/96
YP
295
288
Female
TUM
0.5
04/29/96
YP
256
197
Male
TUM
0.5
04/29/96
YP
255
194
Male
TUM
0.5
04/29/96
YP
255
191
Male
TUM
0.5
04/29/96
YP
244
169
Male
Page 1
-------
Appendix C
Species and River Abbreviations Used
in Tables and Appendices
-------
Appendix C. Species and River Abbreviations Used in Tables and Appendices.
Abbreviations for Soecies
Abbreviations with River Miles
BGS -- Bluegill sunfish
BCM — Bear Creek Mile
CHC — Channel catfish
BuRM — Buffalo River Mile
LMB — Largemouth bass
CCM -- Cedar Creek Mile
RES — Redear sunfish
CRM — Clinch River Mile
SMB -- Smallmouth bass
DRM — Duck River Mile
SPB — Spotted bass
ORM — Ocoee River Mile
STB — Striped bass
SFHRM — South Fork Holston River Mile
YP ~ Yellow Perch
TRM -- Tennessee River Mile
TuRM -- Tuckasegee River Mile
Abbreviations for Rivers and Creeks
BEC — Bear Creek
BUF — Buffalo River
CEC — Cedar Creek
CLI — Clinch River
CLA — Clarks River
DUC -- Duck River
FRE — French Broad River
HIW — Hiwassee River
LBC — Little Bear Creek
LTE ~ Little Tennessee River
NOL -- Nolichucky River
OCO -- Ocoee River
PIG - Pigeon River
SFH — South Fork Holston River
SHO - Shooting Creek
TEN — Tennessee River
TUC — Tuckasegee River
TUM -- Tumbling Creek
WAT - Watauga River
-------
Appendix D
Results of Dioxin Analysis on Channel Catfish
from Selected Reservoirs in 1996
-------
29 8
8 03
13
6 24
377
422
10 2
5 23
10 1
31 8
Wright State University, Dayton, Ohio
Tennessee Valley Authority
2848
Analysis for Total Chlorinated Dioxins and Furans
Results from DB-5 Column
EPA Method 8290
Concentrations Found (picograms per gram of sample or parts-per-tnllion)a
Tetra Tetra Penta
CDFs CDDs CDFs
Penta Hexa Hexa Hepta Hepta Octa Octa Total
CDDs CDFs CDDs CDFs CDDs CDF CDD CDFs
2 93 1.29
798
2.42 2.54 5 02
ND
0.141
0 502 5.07
14
0.716 0 567 ND
0.103
0.835 0 673 1.04 0.479 0 803
ND
0.259
2.92 1 87
1.05 0 802 1.59 1.02 1.19 2.21
ND
0.147
1.3 0 257 3 57
4 09
0.818 0 541 0939
0.512 ND 0.625 ND
0.109 0 239
0.689
ND
0 288
211 1 76
9.79 9.65
189
9.79 89.9 69 3 49.6 22.6 49.9 47.7 218
10 8 10.7 21.2 10.1 100 76 2
57 25 1 56 3 54.2
246
0 882 0.663
1.9 0.54
ND
0.0985
1.22
ND
0.17
1.25
ND
0.257
3.72 2 78
0.873 0.445 0.673 0.436
ND
0.1
0.618
ND
0.226
0.485
ND
0.243
1 7 1.55
1 35 0.855 0.924 0 776
ND
0.101
2.1
ND
0 181
1.36
ND
0 268
2 76 2 27
7 24
1 3
2 81 0.855 0.159 2.12
ND
0.226
3 66
ND
0 243
13 7 10.2
Page 1
-------
Project:
Project Number:
Tennessee Valley Authority
2848
Wright State University. Dayton, Ohio
Analysis for Total Chlorinated Dioxins and Furans
Results from DB-5 Column
EPA Method 8290
Concentrations Found (picograms per gram of sample or parts-per-tnllion)a
TVA
Number
Tetra Tetra Penta
CDFs CDDs CDFs
Penta Hexa Hexa Hepta Hepta Octa Octa
CDDs CDFs CDDs CDFs CDDs CDF CDD
Total Total Total
CDFs CDDs CDDs/CDFs
Wilson Inf
(TRM 272)
1.13 0.741 0.94 0.573
ND
0142
0.772
ND
026
1.13
ND
0.355
2 87
2 07 6 08
8 15
Guntersville FB
(TRM 350)
6.64
1.25 3.89 1.24 013 2.88
ND
0 481
2.66
ND
0 285
5 63
107 137
24 3
Guntersville TZ
(TRM 375)
9.55
1.06 4.34 0.851
ND
0.13
1.88
ND
0.313
2.59
ND
0 341
7.84 13.9 14 2
28 1
Guntersville Inf
(TRM 424)
3 35 1.41 2.98 1.11 0.131
1.99
ND
0.428
1 56
ND
0 25
3 47 6 46 9 54
16
Watts Bar TZ
(TRM 531)
0 505 0.345 0 463 0.536
ND
0.177
0 434
ND
0.302
0 385
ND
0 453
1 47 0 968 3 17
4 14
Watts Bar Inf
(TRM 600)
1.03 1.26
2.6 2.54
ND
0.19
343
ND
0.329
1 39
ND
0.483
3 27 3 63 119
15 5
Watts Bar Inf
(CRM 24)
0 755 0.378 0.808
ND
0.21
0.366 0 897
ND
0.296
0.796
ND
0 42
2 11 1 93 4 18
6 11
LAB BLANK
ND ND ND ND ND ND ND ND ND ND
0 071 0 112 0.118 0.119 0 106 0.139 0.179 0 196 0 272 0.435
LAB BLANK
ND ND ND ND ND ND ND ND ND ND
0 104 0 165 0177 0.211 0166 0.228 0 282 0 328 0 43 0 661
a. The designation ND indicates "None Detected" in excess of the minimum detectable concentration which is listed directly below the ND designation
(2
-------
5 07
2 92
3 57
2 11
47 7
54 2
3 72
1 7
2 76
13 7
2 87
5 63
7 84
Wright State University, Dayton, Ohio
Analysis for 2378-Substituted Chlorinated Dioxins and Furans
Combined Results from DB-5/DB-DIOXIN Columns
EPA Method 8290
Tennessee Valley Authority
2848
Concentrations Found (pieograms per gram of sample or parts-per-trillion)a
2378 2378 12378 23478 12378 123478 123678 123789 234678 123478 123678 123789 1234678 1234789 1234678
TCDF TCDD PeCOF' PeCDF* PeCOD HxCDF* HxCDF* HxCDF* HxCDF' HxCDD HxCDD HxCDD* HpCDF HpCDF HpCDD OCDF
0 936 1 29 ND 3 72 2 42 0 19 0 21 ND ND 0 702 3 58 0 74 ND NO 2 0 502
0 125 0 0817 0 105 0 109 0 198
0 587 0 567 ND ND 0 835 ND ND ND ND ND 1 04 ND ND ND 0 803 ND
0 117 0 701 0 098 0 103 0 101 013 0 191 0 219 0 137 0 247 0 259
ND 0 802 ND 0 801 1 02 ND ND ND ND 0 275 1 6 0 336 ND ND 1 3 0 257
0 329 0 157 0 0917 0 118 0 0949 0 122 0 114 0 206
0 567 0 541 ND ND 0 512 ND ND ND ND ND 0 625 ND ND ND 0 689 ND
0 117 0 0914 0 1 0 106 0 104 0 133 0 172 0 133 0 347 0 335 0 288
9 79 9 65 8 92 10 9 79 24 9 14 6 23 8 26 7 24 6 21 4 23 4 22 6 27 22 6 49 9
10 8 10 7 10 4 10 8 10 1 26 9 16 3 26 7 30 4 27 2 24 1 25 26 9 30 1 25 1 56 3
0 882 0 663 1 34 ND 0 54 ND ND ND ND 0 257 0 748 0 213 ND ND 125 ND
0 091 0 0903 0 0951 0 0934 012 0 579 0 238 0 257
0 785 0 445 ND ND 0 436 ND ND ND ND ND 0 478 0 14 ND ND 0 485 ND
0 119 0 093 0 092 0 0969 0 0952 0 123 0 155 0 422 0 318 0 243
1 18 0 855 ND ND 0 776 ND ND ND ND 0 263 1 54 0 298 ND ND 136 ND
0 115 0 0893 0 0927 0 0977 0 096 0 123 0 141 0 255 0 268
4 97 1 3 ND ND 0 855 ND ND ND ND ND 1 46 0 378 ND ND 3 66 ND
0 108 0 0839 0 174 0 0909 0 0892 0 115 0 146 0 71 0 317 0 243
1 02 0 741 ND 0 94 0 573 ND ND ND ND ND 0 772 ND ND ND 1 13 ND
0 163 0 13 0 137 0 135 0 174 0 249 0 194 0 492 0 364 0 355
3 81 111 ND 1 93 1 24 0 13 ND ND ND 0 54 1 82 0 517 ND ND 2 66 ND
0 132 0 0964 0 135 0 122 3 43 0 675 0 285
5 34 1 06 ND 1 69 0 851 ND ND ND ND 0 546 1 33 ND ND ND 2 59 ND
0 145 0 184 0 184 0 123 0 159 0 585 3 21 0 439 0 341
Page 3
-------
Wright Stata University, Dayton, Ohio
Project
Project Number
Tennessee Valley Authority
2848
Analysis for 2378-Substrtuted Chlorinated Dioxms and Furans
Combined Results from DB-5/D9-DIOXIN Columns
EPA Method 8290
Concentrations Found (ptcograms per gram of sample or parts-per-trilhon)a
TVA 2378 2378 12378 23478 12378 123478 123678 123789 234678 123478 123678 123789 1234678 1234789 1234678
Identification TCDF TCDD PeCDF* PeCDF* PeCDD HxCDF* HxCDF* HxCDF* HxCDF* HxCDD HxCDD HxCDD* HpCDF HpCDF HpCDD OCDF OCDD
Guntersville Inf
(TRM 424)
2 93
1 41
ND
0 118
1 81
1 11
ND
0 0861
ND
0 0907
ND
0 0891
ND
0 115
0 393
1 21
0 383
ND
5 94
ND
06
1 56
ND
0 25
3 47
Watts Bar TZ
(TRM 531)
0 505
0 345
ND
0 199
0 463
0 536
ND
0 162
ND
0 171
ND
0 168
ND
0216
ND
0 27
0 434
ND
021
ND
0 235
ND
0 424
0 385
ND
0 453
1 47
Watts Bar Inf
{TRM 600)
0 495
1 26
ND
0 225
26
254
ND
0 175
ND
0 184
ND
0 181
ND
0 232
0411
3 02
ND
0 377
ND
0 256
ND
0 462
1 39
ND
0 483
3 27
Watts Bar Inf
(CRM 24)
0 755
0 378
ND
0 195
0 808
ND
021
ND
0 16
ND
0 169
ND
0 166
ND
0214
ND
0 302
0 897
ND
0 207
ND
0 23
ND
0415
0 796
ND
0 42
2 11
LAB BLANK
ND
0 071
ND
0 112
ND
0 135
ND
0 105
ND
0 119
ND
0 097
ND
0 102
ND
0 1
ND
0 129
ND
0 163
ND
0 134
ND
0 126
ND
0 139
ND
0 251
ND
0 196
ND
0 272
ND
0 435
LAB BLANK
ND
0 104
ND
0 165
ND
0 202
ND
0 157
ND
0211
ND
0 152
ND
0 16
ND
0 158
ND
0 203
ND
0 266
ND
0 22
ND
0 207
ND
0219
ND
0 396
ND
0 328
ND
0 43
ND
0 661
a The designation ND indicates "None Detected" in excess of the minimum detectable concentration which is listed directly below the ND designation
* These isomers may be convoluted with other isomers of their congener group
-------
95
82
89
81
83
91
82
81
85
84
62
87
67
92
92
Wright State University, Dayton, Ohio
Internal and Surrogate Standards Recoveries
Results from DB-5 Column
Tennessee Valley Authority
2848
%Rec %Rec %Rec %Rec %Rec %Rec %Rec %Rec %Rec
13C-2378 13C-237B 13C-12378 13C-12378 13C-123478 13C-123678 13C-1234678 13C-1234678 13C-OCDD
TCDF TCDD PeCDF PeCDD HxCDF HxCDD HpCDF HpCDD
84
73
72
79
75
83
68
64
72
67
49
82
59
82
87
88
77
75
78
77
82
73
67
76
74
51
84
61
83
87
89
80
84
79
80
86
78
77
85
84
55
85
63
89
90
97
86
93
83
84
94
83
84
92
92
59
89
66
95
96
90
78
87
78
80
89
84
81
86
84
65
88
66
91
88
97
83
95
82
86
96
89
87
93
89
61
94
69
96
95
96
83
92
79
86
94
86
86
84
87
66
87
70
91
91
105
91
102
84
93
102
90
93
93
93
76
93
74
104
100
110
89
98
82
89
96
89
93
89
90
72
85
70
95
95
Page 5
-------
Wright State University, Dayton, Ohio
Internal and Surrogate Standards Recoveries
Results from DB-5 Column
Project:
Project Number:
Tennessee Valley Authority
2848
TVA
Number
TRM 600
CRM 24
LAB BLANK
LAB BLANK
%Rec %Rec %Rec %Rec %Rec %Rec %Rec %Rec %Rec Average
13C-2378 13C-2378 13C-12378 13C-12378 13C-123478 13C-123678 13C-1234678 13C-1234678 13C-OCDD Int %Rec
TCDF TCDD PeCDF PeCDD HxCDF HxCDD HpCDF HpCDD
72
80
54
55
73
87
53
53
81
88
66
67
88
96
88
74
85
88
79
74
93
95
85
77
87
91
83
77
97
100
88
78
93
101
85
80
85
92
76
71
Internal Std
Average Rec
Std Dev
71
+/-11
74
+/-11
79
+/- 9
86
+/-10
82
+1-7
87
+1-9
85
+1-7
92
+/- 9
89
+/- 9
83
P,
-------
Wright State University, Dayton, Ohio
Project
Project Number
Tennessee Valley Authority
2840
Analysis for 2378-Substituted Chlorinated Dioxins and Furans
Combined Results from DB-5/DB-DIOXIN Columns
EPA Method 8290
2.3,7,8-TCDD TEC for the 17 2,3,7,8-Substituted Isomers
Concentrations Found (picograms per gram of sample or parts-per-tnllion)a
TVA
Identification
2378
TCDF
TEF 01
2378 12378 23478
TCDD PeCDF* PeCDF#
12378 123478 123678 123789 234670 123478 123678 123789 1234670 1234789 1234678
PeCDD HxCDF* HxCDF* HxCDF* HxCDF* HxCDD HxCDD HxCDD" HpCDF HpCDF HpCDD
1 0 05 0 5 0 5 0.1 0 1 0 1 0 1 01
0 1
0 1 0 01 0 01 0 01
OCDF
0 001
OCDD
0001
Total
TEC
b
Watts Bar TZ
(TRM 560)
0 0936 1 29
ND 1 86
0 0031
1 21 0019 0021
ND
00041
ND
0 0053
0 0702 0 358 0 074
ND
0 0005
ND
0 001
0 02 0 0005 0 0051 5 03
Melton Hill TZ
(CRM 45)
0 0587 0 567
ND ND
0 0029 0 175
0417
ND
0 0049
ND
0 0052
ND
00051
ND
0 0065
ND
00095
0 104
ND
0 0109
ND
0 0007
ND
0 0012
0 008
ND
0 0001
0 0029 1 38
Ft Loudoun TZ
(TRM 624)
ND
00165
0 002 ND
0 0039
04 0512
ND
0 0046
ND
0 0059
ND
0 0047
ND
00061
0 0275 0 16 0 0336
ND
0 0006
ND
0 001
0 013 0 0003 0 0036
Pickwick FB
(TRM 207)
0 0567 0 541
ND ND
0 0029 0 0228
0.256
ND
0 005
ND
0 0053
ND
0 0052
ND
0 0067
ND
0 0086
0 0625
ND
0 0067
ND
00017
ND
0 0017
0 0069
ND
0 0001
0 0021 0 992
Spike
MS 96/50211
0 979 9 65 0 446
4 9 2 49 1 46 2 38 2 67 2 46 2 14 2 34 0 226 0 27 0 226 0 0499 0 0477 37 7
Spike Duplicate
MSD 96/50211
1 08 10 7 0 52 5 41 5 03 • 2 69 1 63 2 67 3 04 2 72 2 41
2 5 0 269 0 301 0 251 0 0563 0 0542 41 3
Pickwick TZ
(TRM 230)
0 0882 0 663 0 067
ND
0 0227
0 27
ND ND
ND
ND 0 0257 0 0748 0 0213
0 0045 0 0048 0 0047 0 006
ND
ND 0 0125
00029 00012
ND
0 0001
0 0037 1 27
Pickwick Inf
(TRM 259)
0 0785 0 445 ND ND 0 218 ND ND ND ND
0 003 0 0233
ND 0 0478 0 014
0 0046 0 0048 0 0048 0 0061 0 0078
ND
ND 0 0048
00021 00016
ND
0 0001
0 0017 0 868
Pickwick Embay
(Bear Creek Mile 8)
Wilson FB
(TRM 260)
0 110 0 055 ND ND 0 388
0 497 1 3
0 0029 0 0223
ND ND
0 0027 0 021
ND
0 427
ND
ND ND ND 0 0263 0 154 0 0298
0 0046 0 0049 0 0048 0 0062
ND ND
ND
0 0087 0 0045 0 0045 0 0057 0 0073
ND
ND 0 146 0 0370
ND 0 0136
0 0007 0 0013
ND
ND 0 0366
0 0035 0 0016
ND
0 0001
ND
0 0001
0 0028 1 63
0 0137 2 52
Wilson Inf
(TRM 272)
0 102 0 741
ND 0 47
0 0041
0 207
ND ND ND ND
ND 0 0772
0 0065 0 0069 0 0060 0 0007 0 0125
ND ND
ND 00113
0 0097 0 0025 0 0010
ND
0 0002
0 0029 1 75
Page 7
-------
Wright State University, Dayton, Ohio
Project
Project Number
Tennessee Valley Authority
2848
Analysis for 2378-Substrtuted Chlorinated Dioxins and Furans
Combined Results from DB-5/DB-DIOXIN Columns
EPA Method 8290
2,3,7,8-TCDD TEC for the 17 2,3.7,8-Substituted Isomers
Concentrations Found (picograms per gram of sample or parts-per-trilhon)a
TVA
Identification
TEF
2378
TCDF
0 1
2378 12378 23478 12378 123478 123678 123789 234678
TCDD PeCDF* PeCDF* PeCDD HxCDF* HxCDF* HxCDF* HxCDF*
005
05
05
0 1
0 1
0 1
01
123478 123678 123789 1234678 1234789 1234678
HxCDD HxCDD HxCDD" HpCDF HpCDF HpCDD
01
0 1
0 1
001
0 01
001
OCDF OCDD
0 001 0 001
Total
TEC
b
Guntersville FB
(TRM 350)
0 381 1 11
ND
0 0033
0 966 0 622
0013
ND
0 0048
ND
0 0067
ND
0 0061
0 054
0 182
0 0517
ND
0 0172
ND
0 0034
0 0266
ND
0 0001
0 0056
3 45
Guntersville TZ
(TRM 375)
0 534 1 06
ND
0 0036
0 847 0 425
ND
0 0092
ND
0 0092
ND
0 0062
ND
0 0079
0 0546
0 133
ND
0 0292
ND
00161
ND
0 0022
0 0259
ND
0 0002
0 0078
3 17
Guntersville Inf
(TRM 424)
0 293 1 41
ND
0 003
0 905 0 554
ND
0 0043
ND
0 0045
ND
0 0045
ND
0 0057
0 0393
0 121
0 0383
ND
0 0297
ND
0 003
0 0156
ND
0 0001
0 0035
3 43
Watts Bar TZ
(TRM 531)
0 0505 0 345
ND
0 005
0 232 0.268
ND
0 0081
ND
0 0085
ND
00084
ND
00108
ND
0 0135
0 0434
ND
0 0105
ND
0 0012
ND
0 0021
0 0038
ND
0 0002
0 0015
1 01
Watts Bar Inf
(TRM 600)
0 0495 1 26
ND
00056
13 1 27
ND
0 0087
ND
0 0092
ND
0009
ND
00116
0 302
ND
0 0189
ND
00013
ND
0 0023
0 0139
ND
0 0002
0 0033
Watts Bar Inf
(CRM 24)
0 0755 0 378
ND
0 0049
0 404 ND
0 0525
ND
0 008
ND
0 0085
ND
0 0083
ND
0 0107
NO
00151
0 0897
ND
0 0103
ND
0 0011
ND
0 0021
0 008
ND
0 0002
0 0021
1 08
LAB BLANK
ND ND
ND
0 0036 0 0561 0.0034.
ND ND
0 0263 0 0298
ND
0 0049
ND
0 0051
ND
0005
ND
0 0065
ND
0 0081
ND
0 0067
ND
0 0063
ND
0 0007
ND
0 0013
ND
0001
ND
00001
ND
0 0002
LAB BLANK
ND ND
ND
0 0052 0 0826 0 005
ND ND
0 0393 0 0527
ND
0 0076
ND
0 008
ND
0 0079
ND
00101
ND
0 0133
ND
0011
ND
0 0104
ND
0 0011
ND
0 002
ND
0 0016
ND
0 0002
ND
0 0003
a The designation ND indicates "None Detected" in excess of the minimum detectable concentration which Is listed directly below the ND designation
b This is the sum of all 2.3,7,8-substituted TECs The MDLs are counted as 0 5*TEF*MDL for TEC
• These isomers may be convoluted with other isomers of their congener group
B
-------
Project Tennessee Valley Authority
Project Number' 2848
MS 96/50211
2378 2378 12378 23478 12378 123478
TCDF TCDD PeCDF PeCDF PeCDD HxCDF
Quantity found in Spiked sample
0,198 0 195 0 181 0.202 0 198 0 503
Quantity found in Unspiked sample
00115 0011 ND ND 00104 ND
Differenence (Spiked sample - Unspiked sample)
0 187 0 185 0 181 0 202 0 188 0.503
Spike Quantity
02 02 02 02 02 05
Recovery of spike
93% 92% 90% 101% 94% 101%
Average Recovery of all isomers ¦ 94%
MSD 96/5211
2378 2378 12378 23478 12378 123478
TCDF TCDD PeCDF PeCDF PeCDD HxCDF
Quantity found in Spiked sample
0 217 0 214 0 209 0 217 0 202 0 541
Quantity found in Unspiked sample
0 0114 0 0109 ND ND 0 0103 ND
Differenence (Spiked sample - Unspiked sample)
0 206 0 203 0 209 0 217 0 192 0 541
Spike Quantity
02 02 0 2 02 02 05
Recovery of spike
103% 102% 104% 109% 96% 108%
Average Recovery of all isomers - 104%
Wright State University, Dayton, Ohio
Spike Results for 2,3,7.8-Substirtuted Isomers
Results from DB-5 Column
Concentrations Found (nanograms per sample)
123678 123789 234678 123478 123678 123789 1234678 1234789 1234678
HxCDF HxCDF HxCDF HxCDD HxCDD HxCDD HpCDF HpCDF HpCOD OCDF PC DP
0 296 0 482 0 54 0 498 0 433 0 473 0 458 0 546 0 458 1 01 0 965
ND ND ND ND 0 0127 ND ND ND 0 0139 ND 0 0428
0 296 0 482 0 54 0 498 0 42 0 473 0 458 0 546 0 444 1 01 0 922
05 05 05 05 05 05 05 05 05 1 1
59% 96% 108% 100% 84% 95% 92% 109% 89% 101% 92%
123678 123789 234678 123478 123678 123789 1234678 1234789 1234678
HxCDF HxCDF HxCDF HxCDD HxCDD HxCDD HpCDF HpCDF HpCDD OCDF OCDD
0 327 0 536 0 612 0 545 0 484 0 502 0 54 0 606 0 505 113 1 09
ND ND ND ND 0 0126 ND ND ND 0 0138 ND 0 0425
0 327 0 536 0 612 0 545 0 471 0 502 0 54 0 606 0 491 113 105
05 05 05 05 05 05 05 05 05 1 1
65% 107% 122% 109% 94% 100% 108% 121% 98% 113% 105%
-------
Wright State University, Dayton, Ohio
Project:
Project Number:
TVA
Number
Tennessee Valley Authority
2848
Duplicate Samples
Results from DB-5 Column
Concentrations Found (picograms per gram of sample or parts-per-trillion)a
Tetra
CDFs
Tetra
CDDs
Penta
CDFs
Penta
CDDs
Hexa
CDFs
Hexa
CDDs
Hepta
CDFs
Hepta
CDDs
Octa
CDF
Octa
CDD
First sample
MSD 96/50211 108 10.7 21 2 10.1 100 76.2
Second sample
MS 96/50211 9.79 9.65 18.9 9.79
Average 10.3 10.2 20.1 9.92
+/- % difference of samples
5% 5% 6% 1% 5% 5%
Average +/- % difference - 5%
a The designation ND indicates "None Detected" in sample extract.
57
251
89.9 69 3 49 6 22 6
95 2 72 8 53 3 23 9
7%
5%
56.3
49 9
53 1
6%
54.2
47 7
50 9
6%
-------
Appendix E
Recommendations (Preliminary Planning) for
Fish Tissue Studies in 1997
-------
FISH Tir
For Ca
Location
River
This
Free
Species
Resevoi r
Year
River
Mile Studyname
7
Fish?
FORT LOUDOUN
TENNESSEE R
624 LONG-TERM
YE
YES,
CHANNEL CATFISH
APPALACHIA
HIUASSEE R
67.0 RESERVOIR
YE
YES,
LARGEMOUTH BASS
BLUE RIDGE
TOCCOA R
54.0 RESERVOIR
YE
YES,
CHANNEL CATFISH
BLUE RIDGE
TOCCOA R
54.0 RESERVOIR
YE
YES,
LARGEMOUTH BASS
BOONE
WATAUGA R
7.0 RESERVOIR
YE
YES,
CHANNEL CATFISH
BOONE
WATAUGA R
7.0 RESERVOIR
YE
YES,
LARGEMOUTH BASS
BOONE
S FK HOLSTON R
19.0 RESERVOIR
YE
YES,
CHANNEL CATFISH
BOONE
S FK HOLSTON R
19.0 RESERVOIR
YE
YES,
LARGEMOUTH BASS
BOONE
S FK HOLSTON R
27.0 RESERVOIR
YE
YES,
LARGEMOUTH BASS
BOONE
S FK HOLSTON R
27.0 RESERVOIR
YE
YES,
CHANNEL CATFISH
DOUGLAS
FRENCH BROAD R
33.0 RESERVOIR
YE
YES,
LARGEMOUTH BASS
DOUGLAS
FRENCH BROAD R
33.0 RESERVOIR
YE
YES,
CHANNEL CATFISH
DOUGLAS
FRENCH BROAD R
51.0 RESERVOIR
YE
YES,
CHANNEL CATFISH
DOUGLAS
FRENCH BROAD R
51.0 RESERVOIR
YE
YES,
LARGEMOUTH BASS
FORT PATRICK
S FK HOLSTON R
9.0 RESERVOIR
YE
YES,
LARGEMOUTH BASS
FORT PATRICK
S FK HOLSTON R
9.0 RESERVOIR
YE
YES,
CHANNEL CATFISH
¥«,
aiiaiiiipa n i « r « f
-------
R i ver
River
Mile Studyname
This
Year
?
Free
Fish?
ELK R (TRIB. TO
ELIC R (TRIB. TO
TENNESSEE R
TENNESSEE R
TENNESSEE R
TENNESSEE R
TENNESSEE R
TENNESSEE R
OCOEE R
OCOEE R
N FK HOLSTON R
N FK HOLSTON R
PIGEON n
'PIGCON R
EMORY R
EMORY R
BEAR CREEK
BEAR CREEK
HIUASSEE R
HIUASSEE R
ELK R (TRIB. TO
ELK R (TRIB. TO
POWELL R
POWELL R
HOLSTON R
HOLSTON R
CLINCH R
CLINCH R
HIWASSEE R
TENNESSEE R
TENNESSEE R
TENNESSEE R
TENNESSEE R
OCOEE R
6.0 RESERVOIR
6.0 RESERVOIR
277 RESERVOIR
277 RESERVOIR
296 RESERVOIR
296 RESERVOIR
347 RESERVOIR
347 RESERVOIR
3.0 STREAM
3.0 STREAM
4.6 STREAM
4.6 STREAM
7.0 STREAM
7.0 STREAM
14.6 STREAM
14.6 STREAM
27.0 STREAM
27.0 STREAM
38.0 STREAM
38.0 STREAM
41.0 STREAM
41.0 STREAM
65.0 STREAM
65.0 STREAM
110 STREAM
110 STREAM
172 STREAM
172 STREAM
8.0 TARGETED
472 TARGETED
490 TARGETED
529 TARGETED
469 TARGETED
12.0 TARGETED
«-
YE
YE
YE
YE
YE
YE
YE
YE
YE
YE
YE
YE
YE
YE
YE
YE
YE
YE
YE
YE
YES,
YES,
YES,
YES,
YES,
YES,
YES,
YES,
YES,
YES,
YES,
YES,
-¥«r,
YES,
YES,
YES,
YES.
YES,
YES,
YES,
YES,
YES,
YES,
YES,
YES,
YES,
YES,
YES.
YES,
YES,
YES,
YES,
YES,
DATE: 05/251
FISH TISSUE PLANNING REPORT
For Calendar Year : 1997
# Indv Disp Analyze Date
Secies of / Person of for CoU # comments
fish
Comp
Resp.
Fillets
0
SO
M
Comp Coll
LARGEMOUTH BASS
5
C
AL BROUN
ONE TO LAB,
N
N
Y
II 0
CHANNEL CATFISH
5
C
AL BROWN
BOTH TO LAB
r
N
Y
II 0
CHANNEL CATFISH
5
C
AL BROWN
BOTH TO LAB
Y
N
Y
II 0
LARGEMOUTH BASS
5
C
AL BROWN
ONE TO LAB,
N
N
Y
II 0
LARGEMOUTH BASS
5
C
AL BROWN
ONE TO LAB,
N
N
Y
II 0
CHANNEL CATFISH
5
C
AL BROWN
BOTH TO LAB
Y
N
Y
II 0
CHANNEL CATFISH
5
C
AL BROWN
BOTH TO LAB
r
N
Y
II 0
LARGEMOUTH BASS
5
C
AL BROWN
ONE TO LAB,
N
N
Y
II 0
LARGEMOUTH BASS
5
c
CHARLIE
ONE TO LAB,
H
N
Y
II 0
CHANNEL CATFISH
5
c
CHARLIE
BOTH TO LAB
Y
N
Y
II 0
SMALLMOUTH BASS
5
c
CHARLIE
ONE TO LAB,
N
N
Y
II 0
CHANNEL CATFISH
5
c
CHARLIE
BOTH TO LAB
Y
N
Y
II 0
U
II
y
ft~
Tr
T
II 0
CHANNEL CATFI9H-
-5—
—6
CHARLIE
ONE TO LAB,
II u
SMALLMOUTH BASS
5
c
CHARLIE
ONE TO LAB,
N
N
Y
II o
CHANNEL CATFISH
5
c
CHARLIE
BOTH TO LAB
Y
N
Y
/ / 0
CHANNEL CATFISH
5
c
CHARLIE
BOTH TO LAB
Y
N
Y
II 0
LARGEMOUTH BASS
5
c
CHARLIE
ONE TO LAB,
N
N
Y
II 0
CHANNEL CATFISH
5
c
CHARLIE
BOTH TO LAB
Y
N
Y
II o
SMALLMOUTH BASS
5
c
CHARLIE
ONE TO LAB,
N
N
Y
II 0
LARGEMOUTH BASS
5
c
CHARLIE
ONE TO LAB,
N
N
Y
II 0 .
CHANNEL CATFISH
5
c
CHARLIE
BOTH TO LAB
Y
N
Y
II 0
LARGEMOUTH BASS
5
c
CHARLIE
ONE TO LAB,
N
N
Y
II 0
CHANNEL CATFISH
5
c
CHARLIE
BOTH TO LAB
Y
N
Y
II o
CHANNEL CATFISH
5
c
CHARLIE
BOTH TO LAB
Y
N
Y
II o
SMALLMOUTH BASS
5
c
CHARLIE
ONE TO LAB,
N
N
Y
II 0
CHANNEL CATFISH
5
c
CHARLIE
BOTH TO LAB
Y
N
Y
II o
SMALLMOUTH BASS
5
c
CHARLIE
ONE TO LAB,
N
N
Y
II 0
CHANNEL CATFISH
5
c
AL BROUN
ONE TO LAB,
N
Y
N
II 0
CHANNEL CATFISH
5
c
AL BROWN
ONE TO LAB,
N
Y
N
II 0
CHANNEL CATFISH
5
c
AL BROWN
ONE TO LAB,
N
Y
N
II o
CHANNEL CATFISH
5
c
AL BROWN
ONE TO LAB,
N
Y
N
II o
STRIPED BASS
5
c
DON DYCUS
ONE TO LAB,
N
Y
N
II o
CHANNEL CATFISH
5
c
AL BROWN
ONE TO LAB,
N
Y
N
/ ! 0
PAGE:
2
-------
Results from TVA Fish Tissue Studies on Fish Collected Autumn 1995
and Recommendations for Studies in 1996
By: Don L. Dycus
TVA Water Management
May 1996
Introduction/Background
The attached tables summarize results of TVA's fish tissue studies conducted in 1995.
TVA's approach to fish tissue contaminant studies is to first conduct Screening Studies in which
composite samples of an indicator species, such as channel catfish for organics and largemouth
bass for mercury, are examined for a broad array of analytes. Results from Screening Studies are
used to provide direction for future action. If Screening finds low contaminant concentrations,
the site or reservoir would be resampled at the screening level on a rotational basis in 3 to 5 years.
If one or more analytes had somewhat elevated concentrations, that site would be resampled the
next year and samples analyzed for the analyte(s) of concern in a Targeted Screening Study. If
concentrations in Screening efforts or Targeted Screening efforts were sufficiently high to pose
potential human health concerns, the site or reservoir would need to be examined in an Intensive
Study aimed at determining the species affected, the geographical distribution, and year-to-year
variation. Analysis of individual fish (generally 10 replicates) of important species from several
locations provide the data base for examinations. In selected cases, replicate composite samples
could used in Intensive Studies. The assessment phase would continue until the contaminant
concentration was low enough to no longer be a concern or when year-to-year studies indicated
no trend through time. If the former were the case, the site or reservoir would return to the
rotational system. If the latter were the case, a Long-Term Monitoring Study, with either annual
or rotational collections (whichever is appropriate), would be undertaken. The idea for Long-
Term Monitoring is to track the problem analyte so that when concentrations drop below the level
of concern a follow-up Intensive Study can be conducted to document the problem no longer
exists. Generally, composites of indicator species are analyzed for the analyte(s) of concern in
Long-Term Monitoring Studies.
-------
Methods
Details of TVA's collection, processing, and analysis procedures are described in the
report on 1993 fish tissue studies — "Tennessee Valley Reservoir and Stream Quality - 1993; Fish
Tissue Studies in the Tennessee Valley in 1993" by D.L. Williams and D.L. Dycus. The report
was published in July 1994 and is available from:
Water Management Library
Tennessee Valley Authority
1101 Market Street, CST 16B
Chattanooga, TN 37402-2810
(423) 751-7338 or FAX: (423) 751-7648
One noteworthy change for fish tissue studies is that beginning in 1994 more pesticides
were included in the analyses. In addition to the typical list of organochlorine pesticides analyzed,
organophosphate and chlorophenoxy pesticides were analyzed as recommended by the U.S. EPA
in their "Guidance for Assessing Chemical Contaminant Data for Use in Fish Advisories;
Volume 1 Fish Sampling and Analysis" (EPA 823-R-93-007, September 1995). These include
Organochlorine pesticide: dicofol
Organophosphate pesticides: chlorpyrifos, diazinon, disulfoton, ethion, terbufos, and
carbophenothion
Chlorophenoxy pesticide: oxyfluorfen
Summary of Results
Reservoir and rivers included in fish tissue studies in 1995 are listed in Table 1 by
watershed area. Results from the various fish tissue studies conducted in 1995 are summarized
Tables 2-16 and Figures 1 and 2. Physical information such as length and weight for each fish is
in Appendix A, Tables A-l - A-5. Details of study results are available on STORET.
In general, 1995 results were similar to previous years. The most common contaminant of
concern was PCBs. Locations (regardless of study type) with PCB concentrations >0.5 |ig/g are
listed in Table 2. Given the increasing interest in mercury, locations (regardless of study type)
with total mercury >0.40 ng/g are listed in Table 3.
Boxes on the following pages provide highlights of 1995 results and recommendations for
studies in 1996. A detailed list of recommendations for fish tissue studies in 1996 is in
Appendix B. (Note: These recommendations were not final at the time this document was
prepared.) Appendix C contains a news release from the Alabama Department of Public Health
which removed the fish consumption advisory for a portion of Wheeler Reservoir in 1996.
Appendix D contains abbreviations for species and rivers used in tables and appendices.
-------
Screening Studies
Reservoirs and rivers included in Screening Studies in 1995 are listed in Table 1.
Reservoirs: Results are provided in the following tables.
Table 4. Pesticides and PCBs results
Table 5. Metals results
Appendix Table A-l. Collection date, length, weight, etc. for each fish
Results highlights: All pesticides and four of the five metals were either not detected or
found in only low concentrations in all reservoirs sampled. Mercury was the only metal
which was slightly elevated but not sufficiently high to warrant follow-up investigations.
PCBs concentrations were relatively high for three reservoirs. None of these was a
surprise. Ft. Loudoun has a defined PCB problem and was included in screening efforts
because it had not been examined for other analytes for at least three years. Elevated PCB
concentrations in Chickamauga Reservoir have been documented in previous Screening
and Targeted Screening studies, and it appears concentrations generally vary between
0.5 - 1.0 ng/g with highest concentrations at the upper end of the reservoir. The channel
catfish composite from the upstream end of Kentucky Reservoir near Pickwick Dam had a
concentration of 0.8 (j.g/g. Screening studies conducted since 1988 occasionally have
found similar results but no consistent problems have been evident.
Recommendations: None of the above reservoirs need to be resampled until they come
up again in the standard rotation. Several reservoirs have either not been sampled recently
or have not been part of Scrounge efforts recently. Reservoirs to be included in Screening
Studies in 1996 include Pickwick, Wilson, Guntersville, Watts Bar, Melton Hill, Boone,
South Holston, Watauga, Fontana, Hiwassee, Chatuge, Parksville, Bear, Little Bear, and
Cedar. See Appendix B for details about recommended Screening studies for 1996.
Rivers: Results are provided in the following tables.
Table 6. Pesticides and PCBs results
Table 7. Metals results
Appendix Table A-2. Collection date, length, weight, etc. for each fish
Results highlights: All of the pesticides and most metals were either not detected or
found in only low concentrations. Mercury was the only metal and PCBs the only organic
analyte found in sufficient concentrations to be of interest. Sample locations with PCB
concentrations >0.5 are listed in Table 2, and locations with mercury concentrations
>QA\xJg are listed in Table 3.
Recommendations: Six of the river screening sites were sampled for the first time in
1994 and second time in 1995. Four of these (Clarks, Buffalo, Tuckasegee, and Pigeon)
will be resampled in summer 1996. Fish tissue samples were first collected from Bear
Creek in 1995; that site will also be sampled in 1996. Four other sites (Duck, Little
Tennessee, French Broad, and Nolichucky) were not sampled in 1995 and should be in
1996 to take advantage of fish communities studies planned for those sites. Additional
details for 1996 plans are in Appendix B.
-------
Targeted Screening Studies
Reservoirs: Reservoirs sampled in Autumn 1995, including analytes and species of concern:
Wheeler (PCBs - channel catfish)
Nickajack (PCBs - striped bass)
Parksville (PCBs - channel catfish)
Cherokee (PCBs - channel catfish and striped bass/hybrids)
Results are provided in the following tables:
Table 8 ~ PCBs and selected pesticides results
Appendix Table A-3 — Collection date, length, weight, etc. for each fish
Results highlights: Most of the reservoirs listed above were included in Targeted
screening studies in 1994 and 1995 because sampling the preceding year (1993 and 1994)
had shown PCB concentrations were near or above 1.0 |ig/g. This was sufficiently high to
conduct Targeted screening but not so high as to warrant intensive investigations. Results
for 1995 showed PCB concentrations were generally lower than in previous years (below
1.0 ng/g). The exception to this was the striped bass composite from Nickajack Reservoir
which had a concentration of 1.2 ng/g. This is comparable to concentrations found in
previous years. None of the screening studies conducted in 1995 indicated a need for
Targeted Screening studies in 1995.
Recommendations: There are no Targeted Screening studies recommended for 1996.
As stated above, most of these areas have been examined for multiple years with PCB
concentrations varying between about 0.5 and about 1.0 |ig/g. Further Targeted
Screening would likely find comparable results. These areas will be resampled as part of
Reservoir Screening Studies when their turn in rotation comes up.
Rivers: None sampled for Targeted Screening in 1995. Most of the rivers with elevated levels of
mercury and PCBs in Stream Screening studies will be resampled as part of those studies
in 1996.
-------
Intensive Studies
Reservoirs: Reservoirs sampled in 1995, including analytes and species of concern:
Wheeler (DDTr - channel catfish, smallmouth buffalo, and largemouth bass)
Results provided in the following tables:
Table 9 ~ DDTr, chlordane, and PCB results for 1995
Table 10 -- DDTr results for 1991, 1992, 1993, and 1995
Appendix Table A-4 — Collection date, length, weight, etc. for each fish
Objective: -- To determine if decreases in DDTr concentrations observed in 1992 and
1993 had continued, allowing the Alabama Department of Public Health to discontinue a
fish consumption advisory in the Tennessee River portion of Wheeler Reservoir near
Indian Creek Embayment
Study Synopsis: Three replicate composites of each of the three species were collected
at four sites between Tennessee River Miles (TRM) 308 and 325. The Indian Creek
confluence with the Tennessee River is at about TRM 320. Collections efforts were
successful except for a few channel catfish and largemouth bass. Of the 180 fish sought
171 were collected. In addition to composite analysis, the largest individual of each
species from each sample location was analyzed individually to indicate worst-case
conditions. Only two composite samples had a DDTr concentration which exceeded
5.0 ng/g (a smallmouth buffalo composite from TRM 325 had 5.2 (ig/g and another from
TRM 320 had 7.5 ug/g). All other composite samples had concentrations less than
3.0 fig/g with many less than 1.0 (ig/g. DDTr concentrations in the largest individuals of
each species from each site were lower than might be expected. Only three fish had DDTr
concentrations above 5.0 (ig/g (one channel catfish from TRM 315 had 6.1 |ig/g and two
largemouth bass from TRM 320 had 6.3 and 5.3 (ig/g). None of the others even
approached 5.0 (ig/g.
Recommendations: Based on these results, the Alabama Department of Public Health
issued a news release (see Appendix C) in April 1996 which removed the advisory to
avoid eating fish from the Tennessee River. There is no need for further intensive
investigation in this area. It is recommended that TRM 320 (near the mouth of Indian
Creek) be added as a routine collection site when Reservoir Screening studies are
conducted on Wheeler Reservoir (currently expected in 1997).
Rivers: None sampled for Intensive Studies in 1995; none needed in 1996.
-------
Long-Term Monitoring Studies
Reservoirs: Reservoirs sampled in autumn 1995, including analytes and species sampled in 1995:
Tellico (PCBs - channel catfish)
Nickajack (PCBs - channel catfish)
Watts Bar (PCBs - channel catfish)
Fort Loudoun (PCBs - channel catfish)
Results are provided in the following tables:
Table 11 — Tellico, Nickajack, and Watts Bar PCB, DDTr and chlordane results
for 1995
Appendix Table A-5 Tellico, Nickajack, and Watts Bar collection date, length,
weight, etc. for 1995
Other Tables as identified below
Results Highlights: TDEC has issued fish consumption advisories for all these reservoirs
due to PCB contamination. They have all been examined intensively during past years and
are now the Long-Term monitoring phase. None of the results for Long-Term Studies in
1995 would indicate a need to change existing advisories.
Tellico Reservoir (Table 12 and Figure 1) — PCB concentrations in channel
catfish collected in 1995 were relatively high at the forebay sample site and relatively low
at the mid-reservoir sample site compared to results from previous years. There are no
distinct trends except possibly at the forebay site where concentrations have been higher
three of the last four years than in any of the preceding years.
Nickajack Reservoir (Table 13 and Figure 1) — PCB concentrations decreased in
1992 at both locations (especially at the forbay site) compared to previous years (1987 -
1991),and concentrations have tended to remain lower since then, including the 1995
results.
Watts Bar (Table 14 and Figure 1) — PCB concentrations have varyied from year
to year but no trend (either increasing or decreasing) is evident. PCB concentrations in
catfish from Watts Bar Reservoir in 1995 were within the range of concentrations
observed in past studies; again indicating no trend.
Fort Loudoun (Tables 15 and 16 and Figure 2) — Analyses for Long-Term studies
were based on 5-fish composites for all reservoirs except Fort Loudoun where 10
individual catfish were analyzed from the Long-Term, trend site at TRM 624. Individuals
were examined from this site because it is has been monitored longer than any other TVA
site with all previous years based on analysis of individual samples. PCB concentrations
have varied from year to year but no trend (either increasing or decreasing) is evident.
PCB concentrations in catfish from this site in 1995 were within the range of
concentrations observed in past years, again indicating no trend.
Recommendations: Given that fish consumption advisories have been issued for these
reservoirs, these studies will be repeated when fish assemblage sampling is conducted as
part of TVA's Vital Signs Monitoring Program — every other for Tellico, Nickajack, and
Watts Bar and annually for Fort Loudoun.
Rivers: None sampled for Long-Term Monitoring Studies in 1995; none needed in 1996.
-------
Table 1. Listing of Reservoirs and Rivers Included in All Types of Fish Tissue Studies in 1995
Rivers Sampled
Reservoir Sampled
Watershed
River
Type Study
Reservoirs
Type Study
Kentucky Lake Area
Duck River
Pickwick/Wilson Area
Wheeler/Elk Area
Guntersville/Sequatchie Area
Chickamauga/Nickajack Area
Hiwassee River
Clarks
Buffalo
Bear
N/A
Sequatchie
N/A
Ocoee
Ft. Loudoun, Watts Bar, Melton Hill Area N/A
Clinch River
Little Tennessee River
Holston River
Holston
N. Fork Hoi.
Screening
Screening
Screening
Screening
Screening
N/A
Tuckasegee Screening
Screening
Screening
Kentucky
Beech
Normandy
N/A
Wheeler
Tims Ford
N/A
Chickamauga
Nickajack
Parksville
Ft. Loudoun
Watts Bar
N/A
Tellico
Cherokee
Ft. Patrick Henry
Screening
Screening
Screening
Targeted and Intensive
Screening
Screening
Targeted and Long-Term
Targeted
Screening and Long-Term
Long-Term
Long-Term
Targeted
Screening
French Broad River
Pigeon
Screening
N/A
-------
Table 2. Highlights of Autumn 1995 Results from Areas with Advisories and/or "High"
(i.e., >0.5 |ag/g) PCB Concentrations with Comparisons to Results from Those
Areas in 1993 and 1994. All Samples Analyzed as 5-Fish Composites Unless
Otherwise Noted.
Location
Species
1993
1994
1995
Kentucky Reservoir
TRM 30
CHC
NS a
NS
<0.1
TRM 85
CHC
NS
NS
0.3
TRM 206
CHC
NS
NS
0.8
BSRM 7
CHC
NS
NS
0.2
Wheeler Reservoir
TRM 277
CHC
0.5
0.8
0.5
TRM 296
CHC
0.8
1.0
0.6
TRM 347
CHC
1.4
1.3
0.5
ERM 6
CHC
NS
NS
0.2
Nickajack Reservoir
TRM 425
CHC
0.6b
0.7
0.6
TRM 457
CHC
0.7b
0.7
0.6
STB
1.0°
1.2°
1.2
Chick. Reservoir
TRM 472
CHC
NS
NS
0.8
TRM 490
CHC
NS
NS
0.9
TRM 529
CHC
NS0**9
1.0
1.1
HiRM 8
CHC
NS
NS
0.4
Watts Bar Reservoir
TRM 530/1
CHC
ns(doe>
1.0
0.8
SBU
1.4
0.6
NS
TRM 560
CHC
1.2 d
1.0
1.2
SBU
NS
0.4
NS
TRM 600
CHC
1.1"
1.0
1.5
SBU
0.2
0.9
NS
Ft. Loudoun Res.
TRM 603
CHC
NS
NS
0.9
TRM 624
CHC
1.2b
1.6d
1.5b
TRM 652
CHC
NS
NS
1.0
Tellico Reservoir
LTRM 1
CHC
1.4
2.3
2.1
LTRM 15
CHC
1.0
1.1
0.5
Ocoee Reservoir #1
ORM 12
CHC
0.8
1.2
0.4
ORM 16
CHC
1.0
1.7
0.8
Cherokee Reservoir
HRM53
CHC
0.3
0.9
0.5
STB
NS
NS
0.4
HRM76
CHC
<0.1
0.8
0.8
STB
NS
0.4
0.3
a. NS - Not Sampled
b. Average of 10 channel catfish anaylzed individually
c. Average of 10 striped bass analyzed individually
d. Average of 9 channel catfish analyzed individually
-------
Table 3. Highlights of 1995 Results from Reservoir and Stream Locations with "Elevated" (i.e.,
>0.40 ng/g) Total Mercury Concentrations. Note: Black Bass (Largemouth - LMB,
Smallmouth - SMB, and Spotted - SPB) Analysis Were Conducted on Five-fish
Composites and on the Largest of the Five Individuals in the Composite. Channel Catfish
(CHC) Were Analyzed as Five -fish 5 Composites.
Comp./ Weight Mercury
Location Species Ind. (am. if individual-) (Total, ug/g)
RESERVOIRS
Kentucky - Big Sandy River 7
LMB
Ind.
1800
0.40
Tennessee River 85
LMB
Ind.
1775
0.50
Beech - Beech River 36
LMB
Ind.
2800
0.46
Normandy - Duck River 250
LMB
Ind.
2819
0.67
Tims Ford - Elk River 150
LMB
Ind.
1839
0.40
Ft Loudoun - Tennessee River 652
CHC
Comp.
N/A
0.43
LMB
Ind.
2328
0.45
RIVERS
Clarks River Mile 9
CHC
Ind.*
1780
0.45
LMB
Comp.
N/A
0.71
LMB
Ind.
1590
0.87
Buffalo River Mile 17
SMB
Comp.
N/A
0.60
SMB
Ind.
251
0.76
Bear Creek Mile 27
CHC
Comp.
N/A
0.71
Tuckasegee River Mile 15
CHC
Comp.
N/A
0.40
SMB
Comp.
N/A
0.48
SMB
Ind.
633
0.60
Holston River Mile 110
LMB
Comp.
Comp.
0.63
LMB
Ind.
1657
0.78
N. Fork Hoi. River Mile 4
CHC
Comp.
N/A
0.88
SMB
Ind.
1504
1.7
*Only one Channel Catfish was collected from this site.
Note: Additional mercury data are in the following tables and weights for all fish are in the
appendices.
-------
Table 4.
Concentrations (ug/g) of Selected Pesticides and PCBs in Composited Fish
Fillets Collected in 1995 For Reservoir Screening Studies.
For Calendar Year :1995
Collection Site
Spec .%LIPIDS
MIREX
TOXAPH
HEPTA
ALDRIN
BENZ
DDT
DIELD
ENDO
ENDRIN
CHLOR
PCB
BEECH
LAKE
BEE
36. 0
CHC
6.6
<0.008
<0.5
<0. 01
<0.01
<0. 01
0.43
<0.01
<0.01
<0.01
<0.01
0.4
CHICKAMAUGA
HIW
8.0
CHC
8.2
<0.008
<0.5
<0. 01
<0.01
<0. 01
0.10
<0.01
<0. 01
<0.01
<0.01
0.4
TEN
472
CHC
13. 0
<0.008
<0.5
<0. 01
<0.01
<0. 01
0.16
<0.01
<0. 01
<0. 01
<0.01
0.8
TEN
490
CHC
14.0
<0.008
<0.5
<0. 01
<0.01
<0.01
0.17
<0.01
<0.01
<0. 01
<0.01
0.9
TEN
529
CHC
8.7
<0.008
<0.5
<0. 01
<0.01
<0. 01
0.21
<0.01
<0. 01
<0. 01
<0.01
1.1
FORT LOUDOUN
TEN
603
CHC
3.2
<0.008
<0.5
<0. 01
<0.01
<0.01
0.16
<0.01
<0.01
<0. 01
<0.01
0.9
TEN
624
CHC
3.4
<0.008
<0.5
<0. 01
<0.01
<0. 01
0.11
<0.01
<0. 01
<0.01
<0.01
1.5
TEN
652
CHC
4.1
<0.008
<0.5
<0.01
<0.01
<0.01
0. 09
<0.01
<0.01
<0.01
<0.01
1.0
FORT PATRICK HENRY
HOL 9.0
KENTUCKY
CHC
7.8 <0.008
<0.5 <0.01 <0.01
<0.01
0.04 <0.01 <0.01 <0.01 <0.01
0.2
<0.01
<0. 01
<0.01
<0.01
<0.01
<0.01
<0. 01
<0.01
<0. 01
BLU 7 . 0
CHC
2.6
<0.008
<0.5
o
o
V
<0.01
<0.01
0. 10
o
o
<0.01
A
o
o
<0.01
0.2
A
o
o
TEN 30.0
CHC
8.6
<0.008
<0.5
<0. 01
<0.01
<0. 01
0.11
<0.01
<0.01
<0. 01
<0.01
<0.1
<0. 01
TEN 85.0
CHC
8.9
<0.008
<0.5
<0. 01
<0.01
<0.01
0.21
<0. 01
<0. 01
<0. 01
<0.01
0.3
<0. 01
TEN 206
CHC
9.5
<0.008
<0.5
<0.01
<0.01
<0. 01
0. 85
<0. 01
<0. 01
<0. 01
<0.01
0.8
<0. 01
NORMANDY
DUC 250
CHC
3.2
<0.008
<0.5
<0.01
<0.01
<0. 01
<0.010
<0.01
<0. 01
<0. 01
<0.01
<0.1
<0. 01
TIMS FORD
ELK 135
CHC
3.5
<0.008
<0.5
<0.01
<0.01
<0.01
0.08
<0.01
<0.01
<0.01
<0.01
0.2
<0.01
ELK 150
CHC
3.1 <0.008
<0.5 <0.01 <0.01 <0.01 0.06 <0.01 <0.01 <0.01 <0.01
<0.1
<0.01
-------
Table A,
1t.' Concentrations (ug/g) of Selected E Lcides and PCBs in Composited Fish
Fillets
Collected in
1995 For
Reset r
Screening
Studies.
For
Calendar Year :1995
Collection Site
BEECH LAKE
Spec.
%LIPIDS
DURSBAN
DIAZINON
DISULFOTON
ETHION
TERBUFOS
CARBOPHENOTHION
OXYFLUORFEN
BEE 36.0
CHICKAMAUGA
CHC
6.6
<0.01
<0.01
<0. 01
<0.01
<0. 01
<0.01
<0.01
HIW 8.0
CHC
8.2
<0.01
<0.01
<0. 01
<0.01
<0.01
<0. 01
<0.01
TEN 472
CHC
13.0
<0.01
<0. 01
<0. 01
<0. 01
<0. 01
<0.01
<0.01
TEN 490
CHC
14 . 0
<0. 01
<0.01
<0. 01
<0.01
<0.01
<0. 01
<0. 01
TEN 529
FORT LOUDOUN
CHC
8.7
<0.01
<0.01
<0. 01
<0. 01
<0.01
<0.01
<0. 01
TEN 603
CHC
3.2
<0. 01
<0. 01
<0. 01
<0. 01
<0. 01
<0. 01
<0. 01
TEN 624
CHC
3.4
<0.01
<0.01
<0. 01
<0. 01
<0. 01
<0. 01
<0. 01
TEN 652
FORT PATRICK HENRY
CHC
4.1
<0.01
<0.01
<0. 01
<0. 01
<0. 01
<0. 01
<0. 01
HOL 9.0
KENTUCKY
CHC
7.8
<0.01
<0. 01
<0. 01
<0. 01
<0.01
<0. 01
<0. 01
BLU 7.0
CHC
2.6
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0. 01
TEN 30.0
CHC
8.6
<0.01
<0.01
<0. 01
<0. 01
<0. 01
<0.01
<0.01
TEN 85.0
CHC
8.9
t-H
o
o
V
<0. 01
<0. 01
<0. 01
<0.01
<0.01
<0. 01
TEN 206
NORMANDY
CHC
9.5
<0.01
<0.01
<0. 01
<0. 01
<0.01
<0. 01
<0. 01
DUC 250
TIMS FORD
CHC
3.2
<0.01
<0.01
<0.01
A
o
o
h-4
<0. 01
<0.01
<0.01
ELK 135
CHC
3.5
<0.01
<0. 01
<0. 01
<0.01
<0. 01
<0.01
<0. 01
ELK 150
CHC
3.1
<0. 01
<0.01
<0. 01
<0.01
<0.01
<0. 01
<0.01
-------
Table 5. Concentrations (ug/g) of Metals in Composited Fish Fillets Collected
in 1995 for Reservoir Screening Studies.
For Calendar Year :1995
Collection Site Species LABID As Cd Pb Hg Se
BEECH LAKE
BEE
36. 0
CHC
<0. 10
<
0.05
<
0. 02
0.17
0.2
BEE
36. 0
LMB
0. 30
BEE 36.0
IHICKAMAUGA
HIW 8 . 0
LMB
CHC
0.20
<
0.05
<
0. 02
•k
0.46
<0.10
<0.2
HIW
HIW
8.0
8.0
LMB
LMB
0.24
*
0.44
TEN
472
CHC
0.40
<
0. 05
<
0. 02
<0.10
<0.2
TEN
472
LMB
<0.10
TEN
472
LMB
0.22*
TEN
490
CHC
0.28
<
0.05
<
0. 02
<0.10
<0.2
TEN
490
LMB
0. 17
TEN
490
LMB
0.23*
TEN
529
CHC
0.14
<
0.05
<
0. 02
<0.10
<0.2
TEN
529
LMB
0.12
TEN
529
LMB
0.20*
FORT LOUDOUN
TEN
603
CHC
o
rH
o
<
0.05
< 0.02
0.30
<0.2
TEN
603
LMB
0.18
TEN
603
LMB
0.20 *
TEN
624
LMB
0.10
TEN
624
LMB
0.28
TEN
624
CHC
<0.10
<
0.05
< 0.02
0.28
<0.2
TEN
652
CHC
0.20
<
0. 05
0. 06
0.43
<0.2
TEN
652
LMB
0.30
TEN
652
LMB
0.45*
-------
Table :oncentrations (ug/g) of Metals in Comp
Cont -n 1995 for Reservoir Screening Studies
For Calendar Year : 1995
ad Fish Fillets Collected
Collection Site
FORT PATRICK HENRY
Species LABID
As
Cd
Pb
Hg
Se
HOL
9.0
LMB
0.15
HOL
9.0
LMB
0.16*
HOL
9.0
CHC
<0.10
<
0. 05
0.02
<0.10
<0.2
(ENTUCKY
BLU
7 . 0
CHC
<0.10
<
0.05
0.09
<0.10
0.2
BLU
7 . 0
LMB
0.27
BLU
7 . 0
LMB
A
0.40
TEN
30.0
LMB
0.18
TEN
30.0
LMB
*
0.27
TEN
30. 0
CHC
<0.10
<
0. 05
<
0.02
<0.10
<0.2
TEN
85.0
CHC
0.30
<
0. 05
<
0.02
<0.10
0.2
TEN
85.0
LMB
0. 30
TEN
85.0
LMB
*
0. 50
TEN
206
LMB
0.17
TEN
206
LMB
*
0.17
TEN
206
CHC
<0.10
<
0. 05
<
0. 02
0. 34
<0.2
NORMANDY
DUC 250
DUC 250
DUC 250
TIMS FORD
ELK 135
ELK 135
ELK 135
ELK 150
ELK 150
CHC
LMB
LMB
LMB
LMB
CHC
LMB
LMB
<0.10 < 0.05 < 0.02
<0.10 < 0.05
< 0.02
0.25
0.28
0. 67 *
0.20
0.28 *
0.18
0. 35
0.40*
<0.2
<0.2
-------
Table 5. Concentrations (ug/g) of Metals in Composited Fish Fillets Collected
Cont.' 1995 for Reservoir Screening Studies.
For Calendar Year : 1995
Collection Site Species LABID As Cd Pb Hg
ELK 150 CHC <0.10 < 0.05 < 0.02 <0.10
•k
Represents separate analysis of largest individual fish included in the composite.
-------
Talj
Collection Site
BEAR CREEK
BEC 27.3
BUFFALO RIVER
BUF 17.7
HOLSTON RIVER
HOL 110
NFH 4.6
LOWER TENNESSE R
CLA 9.8*
OCOEE RIVER
OCO 2.5
PIGEON RIVER
PIG 8.2
SEQUATCHIE RIVER
SEQ 7.1*
TUCKASEGEE RIVER
TUC 15.0
Concentrations (ug/g) of Selected P
Fillets Collected in 1995 For Strea
~ :ides and PCBs in Composited Fish
•eening Studies.
For Calendar Year : 1995
Spec .%LIPIDS MIREX TOXAPH HEPTA ALDRIN BENZ DDT DIELD ENDO ENDRIN CHLOR
CHC
CHC
CHC
5.5 <0.008 <0.5 <0.01 <0.01 <0.01 <0.010 <0.01 <0.01 <0.01 <0.01
8.7 <0.008 <0.5 <0.01 <0.01 <0.01 <0.010 <0.01 <0.01 <0.01 0.07
PCB DICOFOL
CHC 6.1 <0.008 <0.5 <0.01 <0.01 <0.01 0.07 <0.01 <0.01 <0.01 <0.01 0.2 <0.01
CHC 3.9 <0.008 <0.5 <0.01 <0.01 <0.01 <0.010 <0.01 <0.01 <0.01 <0.01 0.4 <0.01
0.2 <0.01
0.5 <0.01
2.8 <0.008 <0.5 <0.01 <0.01 <0.01 0.05 <0.01 <0.01 <0.01 0.02 0.8 <0.01
CHC 3.2 <0.008 <0.5 <0.01 <0.01 <0.01 <0.010 <0.01 <0.01 <0.01 <0.01 0.2 <0.01
CHC 6.2 <0.008 <0.5 <0.01 <0.01 <0.01 <0.010 <0.01 <0.01 <0.01 <0.01 <0.1 <0.01
CHC 1.4 <0.008 <0.5 <0.01 <0.01 <0.01 <0.010 <0.01 <0.01 <0.01 <0.01 0.5 <0.01
CHC 5.3 <0.008 <0.5 <0.01 <0.01 <0.01 <0.010 <0.01 <0.01 <0.01 <0.01 0.2 <0.01
-------
Table 6. Cont.' Concentrations (ug/g) of Selected Pesticides and PCBs in Composited Fish
Fillets Collected in 1995 For Stream Screening Studies.
Collection Site
BEAR CREEK
BEC 27.3
BUFFALO RIVER
BUF 17.7
HOLSTON RIVER
HOL 110
NFH 4.6
LOWER TENNESSE R
*
CLA 9.8
OCOEE RIVER
OCO 2.5
PIGEON RIVER
PIG 8.2
SEQUATCHIE RIVER
A
SEQ 7.1
TUCKASEGEE RIVER
TUC 15.0
For Calendar Year : 1995
Spec. %LIPIDS DURSBAN DIAZINON DISULFOTON ETHION TERBUFOS CARBOPHENOTHION OXYFLUORFEN
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
6.1 <0.01
3.9 <0.01
5.5
8.7
<0.01
<0.01
2.8 <0.01
3.2 <0.01
6.2 <0.01
1.4 <0.01
5.3 <0.01
<0.01
<0.01
<0. 01
<0. 01
<0.01
<0.01
<0.01
<0. 01
<0. 01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0. 01
<0.01
<0.01
<0.01
<0.01
<0.01
<0. 01
<0.01
<0.01
<0. 01
<0.01
<0.01
<0. 01
<0. 01
<0.01
<0. 01
<0.01
<0. 01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0. 01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
*
Analysis based on only one channel catfish because insufficient fish were collected to comprise a composite.
-------
Table 7 Concentrations (ug/g) of Metals in Com^ id Fish Fillets Collected
Ln 1995 for Stream Screening Studies.
For Calendar Year : 1995
Collection Site Species LAB ID As Cd Pb Hg Se
BEAR CREEK
BEC 27.3 CHC 0.13 < 0.05 < 0.02 0.71 0.3
BEC 27.3 LMB 0.25
BEC 27.3 LMB 0.28*
BUFFALO RIVER
BUF 17.7 CHC <0.10 < 0.05 < 0.02 0.11 <0.2
BUF 17.7 SMB 0.60
•k
BUF 17.7 SMB 0.76
HOLSTON RIVER
HOL 110 CHC <0.10 < 0.05 0.05 0.28 0.2
HOL 110 LMB 0.63
HOL 110 LMB 0.78*
NFH 4.6 CHC <0.10 < 0.05 0.02 0.88 <0.2
NFH 4.6 SMB 1.70**
LOWER TENNESSE R
CLA 9.8 CHC <0.10 < 0.05 < 0.02 0.45** <0.2
CLA 9.8 LMB 0.71
CLA 9.8 LMB 0.87*
OCOEE RIVER
OCO 2.5 CHC <0.10 <0.05 < 0.02 0.13 0.3
OCO 2.5 SPB 0.36
PIGEON RIVER
PIG 8.2 CHC <0.10 < 0.05 < 0.02 0.14 <0.2
PIG 8.2 SMB 0.22
PIG 8.2 SMB 0.29*
SEQUATCHIE RIVER
SEQ 7.1 CHC <0.10 < 0.05 < 0.02 0.16** 0.2
SEQ 7.1 LMB 0.31
-------
Table 7. Concentrations (ug/g) of Metals in Composited Fish Fillets Collected
Cont.' in 1995 for Stream Screening Studies.
For Calendar Year : 1995
Collection Site Species LAB ID As Cd Pb Hg Se
TUCKASEGEE RIVER
TUC
15.0
CHC
<0.10
< 0.05
< 0.02
0.40
<0.2
TUC
15.0
SMB
0.48
TUC
15.0
SMB
*
0. 60
Represents separate analysis of largest individual fish included in the composite.
** Analysis based on only individual because insufficient fish were collected to comprise a composite.
-------
Talj
Concentrations (ug/g) of Selected P
Fillets Collected in 1995 For Targe
For Calendar Year : 1995
cides and PCBs in Composited Fish
(screening Studies.
Collection Site
CHEROKEE
HOL 53.0
HOL 53.0
HOL 53.0
HOL 76.0
HOL 76.0
HOL 76.0
NICKAJACK
TEN 469
PARKSVILLE - OCOEE N
OCO 12.0
OCO 16.0
WHEELER
ELK 6.0
TEN 277
TEN 296
TEN 347
Spec ,%LIPIDS MIREX TOXAPH HEPTA ALDRIN
STB 8.6
STB
CHC
CHC
STB
STB
BENZ
STB
CHC
CHC
CHC
CHC
CHC
CHC
3.6
5.7
8.3
11.0
3.4
5.3
4.3
7.9
6.9
11.0
DDT DIELD ENDO ENDRIN CHLOR
0. 03
0.07
0.23
0. 07
0. 35
<0. 01
0. 02
0. 07
0.78
0. 94
0. 65
<0. 01
<0.01
0. 02
<0.01
<0. 01
<0. 01
<0.01
<0. 01
<0.01
<0.01
<0. 01
PCB DICOFOL
0.4
0.5
0.8
0.4
1.2
0.4
0.8
0.2
0.5
0.6
0.5
-------
Table 9. Concentrations (ug/g) of DDTr, Chlordane, and PCBs in Composited Fish Samples
Collected from Wheeler Reservoir During August 1995 for an Intensive Fish Tissue Study
Location
Species
Lipids
(%)
DDTr
Chlord
PCBs
TRM308
CHC
7.4
1.41
0.02
0.3
TRM308
CHC
5.9
0.61
<0.01
0.5
TRM308
CHC
5.8
1.06
0.02
0.5
TRM308
CHC
1.0
1.33
<0.01
0.4
TRM308
LMB
0.9
0.36
<0.01
<0.1
TRM308
LMB
1.5
0.50
0.02
0.2
TRM308
LMB
1.4
0.24
0.02
0.3
TRM308
LMB
2.0
2.21
<0.01
0.8
TRM308
SBU
16.0
2.30
<0.01
0.5
TRM308
SBU
11.0
1.99
<0.01
0.8
TRM308
SBU
10.0
1.76
<0.01
0.8
TRM308
SBU
20.0
2.02
<0.01
1.4
TRM315
CHC
7.0
2.28
0.02
0.6
TRM315
CHC
5.2
0.47
<0.01
0.5
TRM315
CHC
4.0
0.36
<0.01
0.4
TRM315
CHC
4.5
6.08
<0.01
3.1
TRM315
LMB
0.8
0.36
<0.01
0.3
TRM315
LMB
1.0
0.38
<0.01
0.4
TRM315
LMB
0.8
0.50
<0.01
0.3
TRM315
SBU
8.1
1.43
0.01
<0.1
TRM315
SBU
8.2
1.13
<0.01
0.4
TRM315
SBU
4.5
1.21
<0.01
0.5
TRM315
SBU
7.0
3.38
0.05
1.5
-------
Table 9 cont.
Lipids
Location Species (%)
TRM320 CHC 7.5
TRM 320 CHC 5.6
TRM 320 CHC 7.0
TRM 320 CHC 5.8
TRM 320 LMB 1.6
TRM 320 LMB 2.8
TRM 320 LMB 1.0
TRM 320 LMB 3.4
TRM 320 LMB 7.3
TRM 320 SBU 4.9
TRM 320 SBU 6.5
TRM 320 SBU 9.1
TRM 320 SBU 6.6
TRM 325 CHC 7.1
TRM 325 CHC 5.5
TRM 325 CHC 7.7
TRM 325 CHC 6.4
TRM 325 LMB 1.2
TRM 325 LMB 0.6
TRM 325 LMB 1.5
TRM 325 LMB 1.1
TRM 325 SBU 4.7
TRM 325 SBU 1.3
TRM 325 SBU 6.6
TRM 325 . SBU 5.0
DDTr Chlord PCBs
1.73 <0.01 <0.1
0.35 0.06 <0.1
2.44 <0.01 0.8
1.69 <0.01 0.4
0.60 <0.01 0.3
2.69 <0.01 0.6
0.48 <0.01 0.3
6.33 0.05 1.4
5.33 0.04 1.5
7.50 0.02 1.2
0.96 <0.01 0.3
0.87 <0.01 0.3
3.05 0.03 1.3
0.15 <0.01 <0.1
1.22 <0.01 <0.1
0.19 0.03 <0.1
0.32 <0.01 0.2
0.90 <0.01 0.5
0.25 <0.01 0.3
0.42 <0.01 0.4
0.61 <0.01 0.4
0.67 <0.01 <0.1
1.02 0.02 0.4
5.15 <0.01 0.4
1.62 <0.01 1.2
-------
Table 10. DDTr Concentrations in Fish Collected from Wheeler Reservoir in Vicinity of Indian Creek — 1991,
1992, 1993, and 1995
Smallmouth Buffa
o
Channe
Catfish
^argemouth Bass
TRM
308
TRM
315
TRM
320
TRM
325
TRM
308
TRM
315
TRM
320
TRM
325
TRM
308
TRM
315
TRM
320
TRM
325
1991
Cone. Comp # 1
1.7
4.7
18
5.5
13
3.4
13
2.8
1.2
2.6
5.0
11
Cone. Comp #2
2.8
2.3
20
3.1
7.7
1.9
8.8
2.6
1.0
4.3
6.6
1.6
Cone. Comp #3
2.9
8.5
43
2.2
5.7
7.8
6.1
1.1
0.5
3.1
11
0.1
Mean
2.4
5.2
27
3.5
8.4
4.3
9.4
2.2
0.9
3.3
7.4
4.3
1992
Cone. Comp # 1
1.1
2.6
5.0
9.2
3.1
2.0
1.6
0.6
2.6
7.4
1.9
2.4
Cone. Comp #2
1.2
9.2
3.4
0.9
2.3
2.2
0.7
0.6
7.4
1.5
2.3
Cone. Comp #3
1.5
2.3
2.7
1.7
0.6
2.3
0.3
0.5
1.8
1.3
Mean
1.3
4.7
3.7
3.9
2.0
2.2
0.7
1.2
5.1
1.7
2.0
1993
Cone. Comp U1
0.8
0.4
3.7
7.2
0.8
1.3
1.5
1.5
2.0
2.0
2.5
1.5
Cone. Comp #2
1.1
0.7
13
4.0
0.7
0.7
0.9
0.9
0.5
0.5
1.3
1.1
Cone. Comp #3
1.2
0.9
21
14
0.6
1.7
2.8
0.4
0.3
1.1
0.9
6.4
Mean
1.0
0.6
13
8.4
0.7
1.2
1.7
0.9
0.9
1.2
1.6
3.0
1995
Cone. Comp # 1
2.3
1.4
7.5
0.7
1.4
2.3
1.7
0.2
0.4
0.4
0.6
0.9
Cone. Comp #2
2.0
1.1
1.0
1.0
0.6
0.5
0.4
1.2
0.5
0.4
2.7
0.3
Cone. Comp #3
1.8
1.2
0.9
5.2
1.1
0.4
2.4
0.2
0.2
0.5
0.4
Mean
2.0
1.2
3.1
2.3
1.0
1.0
1.5
0.5
0.4
0.4
1.3
0.5
1995
Individual Analysis
2.0
3.4
3.1
1.6
1.3
6.1
1.7
0.3
2.2
0.5
6.3
5.3
0.6
-------
Tabl^
Concentrations (ug/g) of Selected Pr :ides and PCBs in Composited Fish
Fillets Collected in 1995 For Long Studies.
For Calendar Year : 1995
Collection Site Spec.%LIPIDS MIREX TOXAPH HEPTA ALDRIN BENZ DDT DIELD ENDO ENDRIN CHLOR PCB DICOFOL
NICKAJACK
TEN 425 CHC 11.0 0.10 <0.01 0.6
TEN 457 CHC 13.0 0.09 <0.01 0.6
TELLICO
LTE 1.0 CHC 6.2 0.31 <0.01 2.1
LTE 15.0 CHC 3.1 0.07 <0.01 0.5
WATTS BAR
TEN 531 CHC 7.6 0.11 <0.01 0.8
TEN 560 CHC 3.5 0.13 0.02 1.2
TEN 600 CHC 6.5 0.35 0.06 1.5
-------
Table
Year
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
Summary of PCB Concentrations (ng/g) in Channel Catfish Fillets from Tellico Reservoir, 1985 - 1995
Location
Number
of Fish
Weight
Range (gm)
Mean
Weight (gm)
PCB
Range
Mean PCB
Cone.
LTRM 1
NS
LTRM 11
3-Comp.
328 - 6200
1008
1.0-3.2
2.3
LTRM 1
10-Ind.
444 - 3750
1600
0.2-3.4
1.4
LTRM 11
10-Ind.
330 -3650
1877
0.4-4.2
1.6
LTRM 1
10-Ind.
451 -2902
1110
<0.1 -2.9
0.9
LTRM 11
10-Ind.
331 - 1075
551
0.2-2.2
1.0
LTRM 1
10-Ind.
452 -2481
1092
0.3-4.2
1.6
LTRM 11
10-Ind.
570 -2610
1332
0.1 -2.2
1.2
LTRM 1
10-Ind.
459 - 2593
1024
0.3-4.1
1.6
LTRM 11
10-Ind.
350 -3104
1271
0.1 -2.5
0.9
LTRM 1
¦Comp.
713 - 3347
1771
N/A
1.3
LTRM 11
¦Comp.
1162-2201
1614
N/A
1.5
LTRM 1
•Comp.
477 - 2496
1429
N/A
1.4
LTRM 11
-Comp.
707- 1521
1023
N/A
1.1
LTRM 1
-Comp.
478 -2179
970
N/A
2.7
LTRM 11
-Comp.
807 - 4497
1984
N/A
1.9
LTRM 1
•Comp.
594 - 2094
1389
N/A
1.4
LTRM 15
-Comp.
688 - 2086
1398
N/A
1.0
LTRM 1
-Comp.
667 - 2353
1388
N/A
2.3
LTRM 15
-Comp.
1259-3739
2027
N/A
1.1
LTRM 1
-Comp.
1007 -2684
1411
N/A
2.1
LTRM 15
-Comp.
502 - 1269
776
N/A
0.5
-------
Table 13. Summary of PCB Concentrations (ng/g) in Channel Catfish Fillets from Nickajack Reservoir, 1987 - 1995
Year
Location
Number
Weight
Mean
PCB
Mean PCB
of Fish
Range (gin)
Weight (gm)
Range
Cone.
1987
TRM 425*
1-Comp.
218-2110
1150
N/A
1.9
TRM 457
1-Comp.
636 - 2750
1401
N/A
1.3
1988
TRM 425
10-Ind.
1835 -2705
2175
0.4- 1.9
0.9
TRM 457
3-Ind.
1198-2340
1854
0.9- 1.7
1.3
1989
TRM 425
10-Ind.
346- 1798
1048
0.6-2.0
1.3
TRM 457
10-Ind.
308 - 1001
805
0.6-2.0
0.7
1990
TRM 425
10-Ind.
464 - 2332
1215
0.6- 1.5
1.0
TRM 457
10-Ind.
736 - 2429
1500
0.4- 1.7
1.1
1991
TRM 425
10-Ind.
570-2512
1607
0.3-3.6
1.5
TRM 457
10-Ind.
962 - 2839
2100
0.2-1.9
0.9
1992
TRM 425
10-Ind.
762- 1845
1144
0.1 -0.8
0.4
TRM 457
10-Ind.
883 - 2620
1453
0.1 -0.8
0.5
1993
TRM 425
10-Ind.
650-2359
1293
0.3 - 1.0
0.6
TRM 457
10-Ind.
663 -2141
1259
0.3 - 1.2
0.7
1994
TRM 425
1-Comp.
1023 -2341
1574
N/A
0.7
TRM 457
1-Comp.
975 - 2790
1755
N/A
0.7
1995
TRM 425
1-Comp.
1646-2294
1909
N/A
0.6
TRM 457
1-Comp.
1315-2100
1811
N/A
0.6
* Blue catfish were collected from this site rather than channel catfish
-------
Table 14. Summary of PCB Concentrations (|^g/g) in Channel Catfish Fillets from Watts Bar Reservoir, 1987 - 1995
Year
Location
Number
Weight
Mean
PCB
Mean PCB
of Fish
Range (gm)
Weight (gm)
Range
Cone.
1987
TRM 531
NS
-
-
-
-
TRM 560
6-Ind.
239- 1786
1103
0.1 -4.4
1.4
TRM 600*
10-Ind.
336- 1330
757
0.4-3.1
1.5
1988
TRM 531
10-Ind.
494-4210
1763
0.1 -4.3
1.4
TRM 560
10-Ind.
411 -2765
1124
1.3-7.5
2.7
TRM 600
10-Ind.
829 - 2957
1289
0.8-4.4
2.4
1989
TRM 531 ^
10-Ind.
320- 1695
1033
0.2-1.5
0.8
TRM 560 ^
9-Ind.
324- 1015
544
0.1 -0.5
0.3
TRM 600
7-Ind.
425 - 3229
1437
0.4 - 4.2
1.8
1990
TRM 531
10-Ind.
322-2110
700
<0.1 -2.7
0.6
TRM 560
10-Ind.
282- 1521
838
<0.1 - 1.8
0.8
TRM 600
10-Ind.
208 - 3246
912
0.3 - 5.8
1.6
1991
TRM 531
10-Ind.
899 - 2323
1342
0.8-2,9
1.6
TRM 560
10-Ind.
1149-2812
1571
0.8-4.0
2.3
TRM 600
10-Ind.
466- 1881
967
0.5-4.4
1.4
1992
TRM 531
10-Ind.
407-4178
1514
0.3 - 5.6
1.7
TRM 560
10-Ind.
497-3563
1540
0.2-3.8
1.9
TRM 600
10-Ind.
464-2168
1018
0.4 - 6.2
1.9
1993
TRM 531 DOE
-
-
-
-
TRM 560
9-Ind.
500 - 2590
1086
0.4-2.3
1.2
TRM 600
10-Ind.
442 - 2884
931
0.1 -3.6
1.1
1994
TRM 531
1-Comp.
511 - 2338
1213
N/A
1.0
TRM 560
1-Comp.
523 - 2394
1302
N/A
1.0
TRM 600
1-Comp.
496 - 2348
958
N/A
1.0
1995
TRM 531
1-Comp.
437-2186
1260
N/A
0.8
TRM 560
1-Comp.
800- 1021
907
N/A
1.2
TRM 600
1-Comp.
626 - 2047
1251
N/A
1.5
* Some blue catfish were collected from this site rather than all channel catfish
-------
Table 15. Concentrations (ug/g) of Selected Pesticides and PCBs in Individual Fish Fillets Collected During Autumn 1995 from Fort
Loudoun Reservoir for Long-Term Monitoring.
Location
Species
Collection
Date
Lgt.
(mm)
Wt.
fern)
Sex
Lipid
(%)
DDTr
Chlord
PCBs
TRM624
CHC 1
09/19/95
581
1716
Female
2.9
0.15
<0.01
2.1
TRM 624
CHC 2
09/19/95
456
836
Female
1.5
0.10
0.03
1.2
TRM 624
CHC 3
09/19/95
444
772
Male
4.5
0.14
<0.01
0.8
TRM 624
CHC 4
09/20/95
569
1690
Female
2.4
0.11
0.04
1.9
TRM 624
CHC 5
11/21/95
570
1699
Male
5.7
0.20
0.05
1.2
TRM 624
CHC 6
11/21/95
544
1405
Female
4.2
0.15
<0.01
2.4
TRM 624
CHC 7
11/21/95
490
1026
Male
3.1
0.16
<0.01
1.0
TRM 624
CHC 8
11/21/95
459
764
Female
1.4
0.11
<0.01
0.9
TRM 624
CHC 9
11/21/95
636
2135
Female
2.9
0.11
<0.01
2.7
TRM 624
CHC 10
11/21/95
496
1225
Female
4.1
0.16
0.03
1.1
-------
Table 16. Summary of PCB Concentrations in Channel Catfish, Carp, and White Bass Collected from Fort
Loudoun Reservoir for Period of Record, 1985 - 1995
Location
PCB Range
Mean
No.>2.0
# Fish
TRM
fus/e)
Cue/e)
(ue/e)
Catfish
1985
628
0.2-2.8
1.4
2
10
1987
628
0.1-4.5
1.5
2
10
1988
628
0.2-4.4
1.2
1
10
1989
628
0.6-4.3
2.3
11
20
1990
628
0.3-1.9
1.0
0
10
1991
624
1.4-4.6
2.5
7
10
1992
624
0.1-4.2
1.8
3
9
1993
624
0.4-2.2
1.2
2
10
1994
624
0.6-3.1
1.6
3
9
1995
624
0.8-2.7
1.5
3
10
Carp
1992
651
0.2-0.9
0.6
0
10
White Bass
1987a
628
b
<0.1
a
5
640
b
<0.1
a
5
1992
651
0.3-1.2
0.5
0
10
a. Catfish were sampled from TRMs 624-629. White bass and carp were collected from TRM 651 in 1992.
b. Five white bass were collected from TRMs 628 and 640 in 1987. Each set of five was analyzed as a composite sample.
-------
Figure 1. Average or Composite PCB Concentrations (|ng/g) in Channel Cafish fromTellico,
Nickajack, and Watts Bar Reservoirs for Period of Recored, Collected for Long-Term
Fish Tissue Studies
~ 1985
D1986
~ 1987
~ 1988
B1989
~ 1990
H1991
~ 1992
¦ 1993
H1994
~ 1995
Nickajack Reservoir
TRM 425 TRM 457
B1987
B1988
~ 1989
~ 1990
B1991
~ 1992
B1993
~ 1994
¦ 1995
Watts Bar Reservoir
TRM 530
TRM 560
TRM 600
ftgrph95.doc
-------
Figure 2. Average PCB Concentrations (ng/g) in Channel Cafish from Fort Loudoun
Reservoir for Period of Record, 1985 - 1995
Fort Loudoun Reservoir
TRM624
ftgph95a.doc
-------
Appendix A
Physical Information on All Fish Collected
for Fish Tissue Studies in 1995
* Note: The following tables contain collection date, length, weight, and sex
for each fish included in these studies. Separate tables are provided for each
type of study. For each study, data are grouped by reservoir, river mile and
species. Individuals of the same species which were composited for analysis are
listed in successive order. In Reservoir and Stream Screening Studies
(Tables A-l and A-2, respectively), the largest individual from each
largemouth, smallmouth, or spotted bass composite was also analyzed
separately for mercury. This also was the case for striped bass from Cherokee
Reservoir for the Targeted Screening Study (Table A-3). These fish (i.e.,
those analyzed separately) are identified in these tables by an asterisk (*). Data
for each of these fish are identical to the data for one of the entries above it
because it is the same fish. Fish for the Intensive DDT Study (Table A-4) on
Wheeler Reservoir were handled similarly except the larger individuals were
analyzed separately for DDT. In some cases, more than one fish from a
composite was analyzed separately and in some cases only one fish could be
collected from a site so it had to be analyzed individually. An asterisk (*) is
used in all cases to identify fish analyzed separately as individuals.
-------
Table A-l. Specific Information About Each Fish Collected During 1995 for
Reservoir Screening Fish Tissue Study
For Calendar Year :1995
&
r
ction Site
Date
Species
Length (mm)
Weight(g)
Sex
\
LAKE
BEE
36. 0
09/28/95
LMB
555
2800
Female
BEE
36. 0
10/02/95
LMB
510
2220
Female
BEE
36.0
09/28/95
LMB
515
2220
Female
BEE
36. 0
09/28/95
LMB
451
1220
Female
BEE
36. 0
09/28/95
LMB
401
960
Female
BEE
36.0
09/28/95
LMB *
515
2220
Female
BEE
36.0
09/28/95
A
LMB
555
2800
Female
BEE
36. 0
09/28/95
CHC
494
1280
Male
BEE
36. 0
09/28/95
CHC
593
3000
Female
BEE
36. 0
09/28/95
CHC
666
3440
Male
BEE
36.0
09/28/95
CHC
453
700
Female
BEE
36.0
09/28/95
CHC
426
600
Female
CHICKAMAUGA
HIW
8.0
10/12/95
CHC
684
3707
Female
HIW
8.0
10/12/95
CHC
472
767
Female
HIW
8.0
11/02/95
CHC
480
974
Female
TTTT.1
8.0
11/02/95
CHC
501
1132
Male
1
8.0
11/02/95
CHC
458
717
Female
HIW
8.0
10/12/95
LMB
520
1823
Female
HIW
8.0
10/12/95
LMB
323
414
Female
HIW
8.0
10/12/95
LMB
328
403
Male
HIW
8 . 0
10/12/95
LMB
300
337
Female
HIW
8.0
10/12/95
LMB
296
317
Male
HIW
8.0
10/12/95
LMB*
520
1823
Female
TEN
472
10/10/95
CHC
491
1211
Male
TEN
472
10/10/95
CHC
551
1701
Female
TEN
472
10/10/95
CHC
531
1132
Male
TEN
472
10/10/95
CHC
480
1259
Female
TEN
472
10/10/95
CHC
484
1185
Male
TEN
472
10/10/95
LMB
358
528
Female
TEN
472
10/09/95
LMB
305
312
Male
TEN
472
10/10/95
LMB
528
2369
Female
TEN
472
10/10/95
LMB
437
1126
Female
TEN
472
10/10/95
LMB
315
418
Female
472
10/10/95
LMB*
528
2369
Female
490
10/11/95
LMB
505
1879
Female
TEN
490
10/11/95
LMB
551
2649
Female
-------
Table A-l. Specific Information About Each Fish Collected During 1995 for
Cont.' Reservoir Screening Fish Tissue Study
For Calendar Year :1995
Collection Site
Date
Species
Length(mm)
Weight(g)
Sex
TEN
490
10/10/95
LMB
502
1758
Female
TEN
490
10/10/95
LMB
387
760
Female
TEN
490
10/10/95
LMB
432
955
Female
TEN
490
10/10/95
LMB*
551
2649
Female
TEN
490
10/10/95
CHC
535
1466
Male
TEN
490
10/10/95
CHC
400
600
Male
TEN
490
10/11/95
CHC
547
1659
Female
TEN
490
10/11/95
CHC
556
1631
Female
TEN
490
10/11/95
CHC
490
1274
Female
TEN
529
10/16/95
CHC
637
3159
Male
TEN
529
10/16/95
CHC
445
724
Female
TEN
529
10/16/95
CHC
542
1675
Female
TEN
529
10/16/95
CHC
478
967
Male
TEN
529
10/16/95
CHC
465
806
Male
TEN
529
10/16/95
CHC
0
0
Female
TEN
529
10/16/95
LMB
485
2060
Female
TEN
529
10/16/95
LMB
418
921
Female
TEN
529
10/16/95
LMB
353
574
Female
TEN
529
10/16/95
LMB
349
432
Female
TEN
529
10/16/95
LMB
324
460
Female
TEN
529
10/16/95
LMB*
485
2060
Female
FORT
LOUDOUN
TEN
603
09/19/95
CHC
494
913
Male
TEN
603
09/19/95
CHC
435
793
Male
TEN
603
09/19/95
CHC
595
1644
Male
TEN
603
09/19/95
CHC
494
918
Male
TEN
603
09/19/95
CHC
470
1056
Female
TEN
603
11/06/95
LMB
450
1354
Female
TEN
603
11/06/95
LMB
391
788
Male
TEN
603
11/06/95
LMB
481
1993
Female
TEN
603
11/06/95
LMB
477
1352
Male
TEN
603
11/06/95
LMB
365
712
Male
TEN
603
11/06/95
LMB*
481
1993
Female
TEN
624
09/19/95
LMB
400
1073
Male
TEN
624
09/19/95
LMB
398
1098
Male
TEN
624
09/19/95
LMB
454
1591
Female
TEN
624
09/19/95
LMB
385
820
Female
-------
Table A-l. Specific Information About Each Fish Collected During 1995 for
Cont.' Reservoir Screening Fish Tissue Study
For Calendar Year : 1995
ction Site
624
Date
09/19/95
Species
LMB
Length (mm)
330
Weight(g)
405
Sex
Female
TEN
624
09/19/95
LMB *
454
1591
Female
TEN
624
09/19/95
CHC
581
1716
Female
TEN
624
09/19/95
CHC
456
836
Female
TEN
624
09/19/95
CHC
444
772
Male
TEN
624
09/20/95
CHC
569
1690
Female
TEN
624
11/21/95
CHC
570
1699
Male
TEN
652
09/20/95
CHC
359
362
Male
TEN
652
09/20/95
CHC
497
968
Male
TEN
652
09/20/95
CHC
460
973
Female
TEN
652
09/20/95
CHC
435
663
Female
TEN
652
09/20/95
LMB
370
741
Male
TEN
652
09/20/95
LMB
454
1358
Female
TEN
652
09/20/95
LMB
520
2328
Female
TEN
652
09/20/95
LMB
381
904
Male
TEN
652
09/20/95
LMB
280
331
Male
TEN
652
09/20/95
LMB *
520
2328
Female
PATRICK HENRY
9.0
11/28/95
CHC
445
799
Female
HOL
9.0
11/28/95
CHC
471
937
Male
HOL
9.0
12/12/95
CHC
521
1328
Male
HOL
9.0
11/28/95
LMB
489
2640
Female
HOL
9.0
11/28/95
LMB
4 92
1920
Female
HOL
9.0
11/28/95
LMB
507
2289
Female
HOL
9.0
11/28/95
LMB
425
1351
Female
HOL
9.0
11/28/95
LMB
351
622
Male
HOL
9.0
11/28/95
LMB *
489
2640
Female
ENTUCKY
BLU 7.0
09/21/95
LMB
480
1800
Female
BLU
7.0
09/21/95
LMB
438
1260
Female
BLU
7.0
09/21/95
LMB
342
620
Male
BLU
7.0
09/21/95
LMB
310
420
Female
BLU
7.0
09/21/95
LMB
287
360
Female
BLU
7.0
09/21/95
&
LMB
480
1800
Female
BLU
7.0
09/20/95
CHC
506
980
Female
7.0
09/20/95
CHC
432
600
Female
7.0
09/20/95
CHC
477
1000
Male
BLU
7.0
09/20/95
CHC
412
580
Female
-------
Table
A-l.
Specific
Information About Each
Fish '
Collected
During 3
Cont.
i
Reservoir
Screening
• Fish Tissue
Study
For Calendar
Year :
1995
Collection
Site
Date
Species Length(ram)
Weight(g)
Sex
BLU
7.0
09/20/95
CHC
462
800
Female
TEN
30. 0
11/06/95
CHC
545
1910
Female
TEN
30.0
11/06/95
CHC
491
1255
Male
TEN
30. 0
11/06/95
CHC
463
1060
Female
TEN
30.0
11/06/95
CHC
465
955
Female
TEN
30. 0
11/06/95
CHC
451
940
Female
TEN
30. 0
09/19/95
LMB
409
1200
Female
TEN
30.0
09/19/95
LMB
401
1160
Male
TEN
30. 0
09/19/95
LMB
465
1600
Female
TEN
30. 0
09/19/95
LMB
380
920
Male
TEN
30. 0
09/19/95
LMB
383
820
Male
TEN
30. 0
09/19/95
LMB *
465
1600
Female
TEN
85.0
09/20/95
LMB
396
1000
Male
TEN
85.0
11/09/95
LMB
478
1420
Female
TEN
85.0
11/09/95
LMB
413
990
Male
TEN
85. 0
11/09/95
LMB
485
1775
Male
TEN
85. 0
11/09/95
LMB
367
805
Female
TEN
85.0
11/09/95
*
LMB
485
1775
Male
TEN
85.0
09/22/95
CHC
450
980
Male
TEN
85.0
09/22/95
CHC
450
960
Male
TEN
85. 0
09/22/95
CHC
410
780
Female
TEN
85. 0
09/22/95
CHC
506
1080
Male
TEN
85. 0
09/22/95
CHC
430
760
Male
TEN
206
09/18/95
CHC
516
1360
Male
TEN
206
11/09/95
CHC
609
2745
Male
TEN
206
11/15/95
CHC
505
1455
Female
TEN
206
09/18/95
LMB
376
1000
Female
TEN
206
09/18/95
LMB
324
640
Female
TEN
206
09/18/95
LMB
331
580
Female
TEN
206
09/18/95
LMB
423
1300
Male
TEN
206
09/18/95
LMB
356
860
Female
TEN
206
09/18/95
LMB *
423
1300
Male
NORMANDY
DUC
250
09/25/95
CHC
530
1191
Male
DUC
250
09/25/95
CHC
468
763
Male
DUC
250
09/25/95
CHC
439
615
Female
DUC
250
09/25/95
CHC
658
430
Male
LABID
-------
Table A-l. Specific Information About Each Fish Collected During 1995 for
Cont.' Reservoir Screening Fish Tissue Study
For Calendar Year :1995
ection Site
Date
Species
Length(mm)
Weight(g)
Sex
-
250
09/25/95
CHC
475
928
Female
DUC
250
09/25/95
LMB
395
891
Female
DUC
250
09/25/95
LMB
343
591
Female
DUC
250
09/25/95
LMB
558
2819
Female
DUC
250
09/25/95
LMB
303
424
Female
DUC
250
11/17/95
LMB
427
1119
Female
DUC
250
09/25/95
LMB*
558
2819
Female
IMS :
FORD
ELK
135
11/15/95
CHC
453
821
Male
ELK
135
11/15/95
CHC
532
1585
Female
ELK
135
11/15/95
CHC
380
419
Male
ELK
135
11/15/95
CHC
373
401
Male
ELK
135
11/15/95
CHC
475
915
Male
ELK
135
09/27/95
LMB
449
1342
Male
ELK
135
09/27/95
LMB
508
1872
Female
ELK
135
09/27/95
LMB
377
678
Female
ELK
135
09/27/95
LMB
425
1069
Female
135
09/27/95
LMB
385
713
Male
135
09/27/95
LMB*
508
1872
Female
ELK
150
09/27/95
CHC
474
813
Male
ELK
150
11/15/95
CHC
449
753
Male
ELK
150
11/15/95
CHC
443
749
Male
ELK
150
11/15/95
CHC
442
603
Male
ELK
150
11/15/95
CHC
500
910
Male
ELK
150
09/26/95
LMB
448
1116
Female
ELK
150
09/26/95
LMB
477
1839
Female
ELK
150
09/26/95
LMB
431
1085
Male
ELK
150
09/26/95
LMB
465
1471
Female
ELK
150
09/26/95
LMB
382
864
Female
ELK
150
09/26/95
LMB *
477
1839
Female
-------
Table A-2. Specific Information About Each Fish Collected During 1995 for
Stream Screening Fish Tissue Study
For Calendar Year : 1995
f
ction Site
Date
Species
Length(mm)
Weight(g)
Sex
CREEK
BEC
27.3
05/23/95
LMB
326
371
Female
BEC
27.3
05/23/95
LMB
290
335
Female
BEC
27.3
05/23/95
LMB
355
681
Female
BEC
27.3
05/23/95
LMB *
355
681
Female
BEC
27.3
05/23/95
CHC
431
661
Female
BEC
27.3
05/23/95
CHC
354
366
Male
BEC
27.3
05/23/95
CHC
484
1103
Male
SUFFALO RIVER
BUF
17.7
07/25/95
SMB
250
193
Female
BUF
17.7
07/25/95
SMB
265
206
Female
BUF
17 .7
07/25/95
SMB
271
206
Female
BUF
17.7
07/25/95
SMB
274
244
Female
BUF
17.7
07/25/95
SMB
284
251
Female
BUF
17.7
07/25/95
SMB *
284
251
Female
BUF
17.7
07/25/95
CHC
440
736
Male
BUF
17.7
07/25/95
CHC
414
587
Male
17.7
07/25/95
CHC
430
745
Female
17.7
07/25/95
CHC
433
699
Male
BUF
17.7
07/25/95
CHC
446
750
Male
[OLSTON RIVER
HOL
110
07/10/95
LMB
395
997
Female
HOL
110
07/10/95
LMB
294
393
Female
HOL
110
07/11/95
LMB
459
1657
Female
HOL
110
07/11/95
LMB
346
536
Female
HOL
110
07/11/95
LMB
341
536
Female
HOL
110
07/11/95
LMB*
459
1657
Female
HOL
110
07/10/95
CHC
508
1377
Female
HOL
110
07/10/95
CHC
466
1009
Male
HOL
110
07/10/95
CHC
494
1297
Female
HOL
110
07/10/95
CHC
493
1307
Male
HOL
110
07/10/95
CHC
525
1204
Male
NFH
4.6
07/13/95
CHC
574
2038
Female
NFH
4 . 6
07/13/95
CHC
463
1002
Female
NFH
4.6
07/13/95
CHC
556
1551
Female
4.6
07/13/95
CHC
453
823
Male
4.6
07/13/95
CHC
455
854
Female
NFH
4.6
07/13/95
SMB*
481
1504
Male
-------
Table A-2. Specific Information About Each Fish
Cont.' Stream Screening Fish Tissue Study
For Calendar Year
Collected During 1995 for
Collection Site
LOWER TENNESSE R
Date
: 1995
Species Length(mm) Weight(g)
Sex
CLA
9.8
08/29/95
LMB
416
1129
Female
CLA
9.8
08/29/95
LMB
456
1590
Female
CLA
9.8
08/29/95
LMB
425
1280
Female
CLA
9.8
08/29/95
LMB
423
1319
Female
CLA
9.8
08/29/95
LMB
366
759
Female
CLA
9.8
08/29/95
LMB *
456
1590
Female
CLA
9.8
08/29/95
CHC
585
1780
Female
CLA
9.8
08/29/95
CHC
585
1780
Female
OCOEE
OCO
RIVER
2.5
06/20/95
SPB *
383
694
Female
OCO
2.5
06/20/95
CHC
410
485
Female
OCO
2.5
06/20/95
CHC
439
618
Female
OCO
2.5
06/20/95
CHC
429
670
Male
OCO
2.5
06/20/95
CHC
420
592
Female
OCO
2.5
06/20/95
CHC
423
601
Female
PIGEON
PIG
RIVER
8.2
07/13/95
CHC
418
547
Female
PIG
8.2
07/13/95
CHC
368
448
Female
PIG
8.2
07/13/95
CHC
359
400
Male
PIG
8.2
07/13/95
CHC
370
395
Female
PIG
8.2
07/13/95
CHC
328
281
Female
PIG
8.2
07/13/95
SMB
360
658
Female
PIG
8.2
07/13/95
SMB
450
1155
Female
PIG
8.2
07/13/95
SMB
470
1481
Female
PIG
8.2
07/13/95
SMB
336
489
Female
PIG
8.2
07/13/95
SMB
304
436
Female
PIG
8.2
07/13/95
SMB *
470
1481
Female
SEQUATCHIE RIVER
SEQ 7.1
06/06/95
LMB *
365
614
Male
SEQ
7.1
06/06/95
CHC
453
734
Female
SEQ
7.1
06/06/95
CHC
478
846
Female
TUCKASEGEE RIVER
TUC 15.0
07/20/95
SMB
347
626
Male
TUC
15.0
07/20/95
SMB
318
569
Male
TUC
15.0
07/20/95
SMB
350
633
Female
TUC
15.0
07/20/95
SMB
305
430
Female
TUC
15.0
07/20/95
SMB
357
633
Female
LABID
-------
Table A-2. Specific Information About Each Fish Collected During 1995 for
Cont.' Stream Screening Fish Tissue Study
For Calendar Year : 1995
ction Site
Date
Species
Length(mm)
Weight(g)
Sex
15.0
07/20/95
SMB*
357
633
Female
TUC
15.0
09/28/95
CHC
464
963
Male
TUC
15.0
09/28/95
CHC
449
755
Male
TUC
15.0
09/28/95
CHC
459
908
Female
TUC
15.0
09/28/95
CHC
419
728
Female
TUC
15.0
09/28/95
CHC
530
1692
Female
-------
Table A-3. Specific Information About Each Fish Collected During 1995 for
Targeted Fish Tissue Study
For Calendar Year :
1995
ction Site
Date
Species
Length(mm)
Weight(g)
Sex
KEE
HOL
53.0
09/28/95
CHC
460
832
Male
HOL
53. 0
12/12/95
CHC
461
780
Male
HOL
53.0
12/15/95
CHC
405
534
Female
HOL
53.0
12/15/95
CHC
455
790
Male
HOL
53.0
12/15/95
CHC
371
436
Male
HOL
53. 0
09/28/95
STB
674
2952
Female
HOL
53. 0
09/28/95
STB
675
29 42
Female
HOL
53. 0
09/28/95
STB
575
1879
Male
HOL
53.0
09/28/95
STB
503
1447
Female
HOL
53. 0
09/28/95
STB
501
1346
Female
HOL
53. 0
09/28/95
STB *
674
2952
Female
HOL
76.0
09/27/95
CHC
455
712
Male
HOL
76.0
09/29/95
CHC
412
598
Female
HOL
76.0
09/29/95
CHC
503
980
Female
HOL
76.0
09/29/95
CHC
558
1723
Female
HOL
76.0
09/29/95
CHC
459
872
Female
|
76.0
09/29/95
STB
556
1918
Female
1
76.0
09/29/95
STB
449
1061
Male
HOL
76. 0
12/08/95
STB
689
3836
Male
HOL
76.0
12/08/95
STB
601
2782
Male
HOL
76.0
12/08/95
STB
641
3084
Male
HOL
76.0
12/08/95
STB *
689
3836
Male
NICKAJACK
TEN
469
11/16/95
STB
700
4163
Female
TEN
469
11/16/95
STB
842
8703
Female
TEN
469
11/17/95
STB
823
7840
Male
TEN
469
11/17/95
STB
688
4568
Female
TEN
469
11/17/95
STB
873
8882
Female
PARKSVILLE - OCOEE N
OCO
12. 0
10/18/95
CHC
465
810
Male
OCO
12.0
10/18/95
CHC
473
560
Male
OCO
12.0
10/18/95
CHC
437
670
Female
OCO
12.0
10/19/95
CHC
4 62
774
Male
OCO
12.0
10/19/95
CHC
446
714
Male
—
16.0
10/20/95
CHC
516
1224
Male
16. 0
10/20/95
CHC
470
881
Female
OCO
16.0
10/20/95
CHC
610
2075
Male
-------
Table
A-3.
Specific
Information About
Each Fish Collected During '
Cont.
»
Targeted Fish Tissue Study
For Calendar Year :
1995
Collection
Site
Date
Species
Length(mm)
Weight(g)
Sex
OCO
16.0
10/20/95
CHC
513
1220
Female
OCO
16.0
10/20/95
CHC
497
1150
Female
WHEELER
ELK
6.0
10/03/95
CHC
483
1080
Male
ELK
6.0
10/03/95
CHC
466
1040
Female
ELK
6.0
11/22/95
CHC
470
890
Female
ELK
6.0
11/22/95
CHC
380
395
Female
ELK
6.0
11/22/95
CHC
362
310
Female
TEN
277
10/02/95
CHC
547
2060
Female
TEN
277
10/02/95
CHC
516
1440
Male
TEN
277
10/02/95
CHC
475
840
Female
TEN
277
10/02/95
CHC
431
680
Female
TEN
277
10/02/95
CHC
456
1950
Male
TEN
296
12/05/95
CHC
643
3245
Female
TEN
296
12/05/95
CHC
564
2090
Female
TEN
296
12/05/95
CHC
496
1340
Male
TEN
296
12/04/95
CHC
451
805
Male
TEN
296
12/05/95
CHC
481
1055
Male
TEN
347
10/11/95
CHC
457
975
Female
TEN
347
10/11/95
CHC
520
1735
Female
TEN
347
10/11/95
CHC
455
985
Male
TEN
347
10/11/95
CHC
560
1885
Male
TEN
347
10/11/95
CHC
434
840
Male
-------
Table A-4. Specific Information About Each Fish Collected During 1995 for
Intensive Fish Tissue Study
For Calendar Year :1995
ction Site
Date
Species
Length(mm)
Weight(g)
Sex
ER
TEN
308
08/28/95
SBU
670
4784
Female
TEN
308
08/28/95
SBU
632
3850
Male
TEN
308
08/28/95
SBU
456
2182
Male
TEN
308
08/28/95
SBU
518
2617
Male
TEN
308
08/28/95
SBU
660
5232
Female
TEN
308
08/28/95
SBU
528
2122
Male
TEN
308
08/28/95
SBU
535
2711
Male
TEN
308
08/28/95
SBU
528
2573
Male
TEN
308
08/28/95
SBU
518
2348
Male
TEN
308
08/28/95
SBU
541
2382
Male
TEN
308
08/28/95
SBU
606
5541
Female
TEN
308
08/28/95
SBU
630
4092
Female
TEN
308
08/28/95
SBU
559
2611
Male
TEN
308
08/28/95
SBU
541
2420
Male
TEN
308
08/28/95
SBU
618
3289
Male
TEN
308
08/28/95
SBU*
606
5541
Female
308
08/28/95
CHC
454
868
Male
308
08/28/95
CHC
371
458
Male
TEN
308
08/28/95
CHC
496
1133
Female
TEN
308
08/28/95
CHC
421
548
Male
TEN
308
08/28/95
CHC
545
1740
Female
TEN
308
08/28/95
CHC
610
1800
Male
TEN
308
08/28/95
CHC
430
799
Male
TEN
308
08/28/95
CHC
600
1843
Male
TEN
308
08/28/95
CHC
416
587
Male
TEN
308
08/28/95
CHC
528
1596
Male
TEN
308
08/28/95
CHC
425
760
Female
TEN
308
08/28/95
CHC
576
1966
Female
TEN
308
08/28/95
CHC
605
2079
Male
TEN
308
08/29/95
CHC
593
1868
Male
TEN
308
08/29/95
CHC
576
1504
Male
TEN
308
08/28/95
CHC*
605
2079
Male
TEN
308
08/29/95
LMB
308
379
Male
TEN
308
08/29/95
LMB
314
427
Male
308
08/29/95
LMB
310
362
Female
308
08/29/95
LMB
351
525
Female
-------
Table A-4. Specific Information About Each Fish
Cont.1 Intensive Fish Tissue Study
For Calendar Year
Collected During 1995 for
1995
Election Site
Date
Species
Length(mm)
Weight(g)
Sex
TEN
308
08/29/95
LMB
307
354
Male
TEN
308
08/29/95
LMB
329
363
Male
TEN
308
08/29/95
LMB
535
2619
Female
TEN
308
08/29/95
LMB
300
332
Male
TEN
308
08/29/95
LMB
287
313
Female
TEN
308
08/29/95
LMB
316
412
Male
TEN
308
08/29/95
LMB
342
501
Male
TEN
308
08/29/95
LMB
290
345
Male
TEN
308
08/29/95
LMB
351
637
Female
TEN
308
08/29/95
LMB
316
417
Male
TEN
308
08/29/95
LMB
268
268
Female
TEN
308
08/29/95
LMB *
535
2619
Female
TEN
315
08/23/95
LMB
325
290
Male
TEN
315
08/23/95
LMB
291
304
Male
TEN
315
08/24/95
LMB
426
1011
Male
TEN
315
08/24/95
LMB
308
366
Female
TEN
315
08/24/95
LMB
402
804
Male
TEN
315
08/24/95
LMB
326
416
Male
TEN
315
08/24/95
LMB
294
260
Male
TEN
315
08/29/95
LMB
310
410
Male
TEN
315
08/29/95
LMB
416
931
Female
TEN
315
08/24/95
LMB *
426
1011
Male
TEN
315
08/24/95
CHC
568
1902
Female
TEN
315
08/24/95
CHC
552
767
Female
TEN
315
08/28/95
CHC
463
1056
Female
TEN
315
08/28/95
CHC
486
1150
Female
TEN
315
08/28/95
CHC
473
884
Male
TEN
315
08/28/95
CHC
400
451
Male
TEN
315
08/28/95
CHC
472
1109
Female
TEN
315
08/30/95
CHC
413
513
Female
TEN
315
08/30/95
CHC
491
848
Female
TEN
315
08/30/95
CHC
607
1569
Male
TEN
315
08/30/95
CHC
570
1504
Male
TEN
315
08/30/95
CHC
558
1735
Male
TEN
315
08/30/95
CHC
522
1403
Male
TEN
315
08/24/95
CHC*
568
1902
Female
TEN
315
08/23/95
SBU
450
1257
Male
LABID
-------
Table A-4 Specific Information About Each Fish Collected During 1995 for
Cont.' Intensive Fish Tissue Study
For Calendar Year :1995
it
=tion Site
Date
Species
Length(mm)
Weight(g)
Sex
315
08/23/95
SBU
430
1054
Male
TEN
315
08/23/95
SBU
450
1224
Male
TEN
315
08/23/95
SBU
510
1963
Female
TEN
315
08/24/95
SBU
464
1455
Male
TEN
315
08/24/95
SBU
450
1216
Male
TEN
315
08/24/95
SBU
466
1576
Male
TEN
315
08/24/95
SBU
464
1435
Female
TEN
315
08/24/95
SBU
510
2230
Male
TEN
315
08/24/95
SBU
495
2068
Male
TEN
315
08/28/95
SBU
492
1806
Male
TEN
315
08/28/95
SBU
340
512
Female
TEN
315
08/28/95
SBU
324
461
Male
TEN
315
08/28/95
SBU
565
2982
Male
TEN
315
08/28/95
SBU
451
1191
Male
TEN
315
08/28/95
SBU*
565
2982
Male
TEN
320
08/22/95
SBU
455
1352
Male
TEN
320
08/22/95
SBU
495
1700
Female
320
08/22/95
SBU
551
2273
Male
320
08/22/95
SBU
505
1672
Female
TEN
320
08/23/95
SBU
480
1715
Male
TEN
320
08/23/95
SBU
540
2343
Female
TEN
320
08/28/95
SBU
485
1598
Male
TEN
320
08/28/95
SBU
535
2420
Female
TEN
320
08/28/95
SBU
526
2044
Male
TEN
320
08/28/95
SBU
447
1366
Female
TEN
320
08/28/95
SBU
574
2743
Female
TEN
320
08/30/95
SBU
535
2468
Female
TEN
320
08/30/95
SBU
362
707
Male
TEN
320
08/30/95
SBU
420
1079
Male
TEN
320
08/30/95
SBU
499
1820
Female
TEN
320
08/28/95
SBU*
574
2743
Female
TEN
320
08/22/95
CHC
454
849
Male
TEN
320
08/22/95
CHC
490
1156
Female
TEN
320
08/23/95
CHC
502
1152
Female
TTTM
320
08/23/95
CHC
483
901
Female
320
08/24/95
CHC
476
924
Female
1 IjlN
320
08/24/95
CHC
455
954
Male
-------
Table A-4. Specific Information About Each Fish Collected During 1995 for
Cont.' Intensive Fish Tissue Study
For Calendar Year :1995
Collection Site
Date
Species
Length(mm)
Weight(g)
Sex
TEN
320
08/24/95
CHC
547
1459
Female
TEN
320
08/28/95
CHC
468
911
Female
TEN
320
08/28/95
CHC
315
304
Male
TEN
320
08/28/95
CHC
383
507
Female
TEN
320
08/28/95
CHC
460
822
Male
TEN
320
08/28/95
CHC
505
1378
Male
TEN
320
08/28/95
CHC
538
1566
Female
TEN
320
08/30/95
CHC
519
1010
Female
TEN
320
08/30/95
CHC
558
1702
Female
TEN
320
08/30/95
CHC*
558
1702
Female
TEN
320
08/22/95
LMB
360
597
Male
TEN
320
08/23/95
LMB
315
390
Male
TEN
320
08/23/95
LMB
332
485
Female
TEN
320
08/23/95
LMB
345
472
Male
TEN
320
08/23/95
LMB
343
494
Female
TEN
320
08/23/95
LMB
318
435
Male
TEN
320
08/23/95
LMB
304
330
Male
TEN
320
08/23/95
LMB
290
323
Male
TEN
320
08/23/95
LMB
530
2004
Male
TEN
320
08/23/95
LMB
493
1916
Male
TEN
320
08/24/95
LMB
300
358
Male
TEN
320
08/24/95
LMB
358
644
Female
TEN
320
08/24/95
LMB
350
528
Male
TEN
320
08/24/95
LMB
324
410
Female
TEN
320
08/24/95
LMB
360
551
Male
TEN
320
08/23/95
LMB*
530
2004
Male
TEN
320
08/23/95
LMB *
493
1916
Male
TEN
325
08/21/95
LMB
300
339
Male
TEN
325
08/21/95
LMB
350
589
Male
TEN
325
08/21/95
LMB
310
343
Male
TEN
325
08/21/95
LMB
359
598
Male
TEN
325
08/21/95
LMB
321
386
Female
TEN
325
08/21/95
LMB
313
375
Male
TEN
325
08/22/95
LMB
391
735
Female
TEN
325
08/22/95
LMB
277
278
Female
TEN
325
08/22/95
LMB
290
331
Male
TEN
325
08/22/95
LMB
289
257
Female
-------
•Table A-4. Specific Information About Each Fish Collected During 1995 for
Cont.' Intensive Fish Tissue Study
For Calendar Year : 1995
;tion Site
Date
Species
Length(mm)
Weight(g)
Sex
325
08/22/95
LMB
501
1888
Male
TEN
325
08/23/95
LMB
355
556
Male
TEN
325
08/23/95
LMB
475
1615
Male
TEN
325
08/23/95
LMB
300
290
Male
TEN
325
08/23/95
LMB
365
755
Female
TEN
325
08/22/95
LMB*
501
1888
Male
TEN
325
08/22/95
CHC
475
911
Female
TEN
325
08/28/95
CHC
425
977
Female
TEN
325
08/28/95
CHC
394
451
Female
TEN
325
08/28/95
CHC
557
800
Male
TEN
325
08/30/95
CHC
485
1004
Female
TEN
325
08/30/95
CHC
474
1032
Female
TEN
325
08/30/95
CHC
538
1086
Male
TEN
325
08/30/95
CHC
439
717
Male
TEN
325
08/30/95
CHC
491
1129
Male
TEN
325
08/30/95
CHC
474
927
Female
TEN
325
08/30/95
CHC
599
1852
Male
325
08/30/95
CHC
475
1039
Male
XX.1N
325
08/30/95
CHC
471
902
Female
TEN
325
08/30/95
CHC
402
643
Female
TEN
325
08/30/95
CHC*
599
1852
Male
TEN
325
08/21/95
SBU
455
1243
Male
TEN
325
08/21/95
SBU
486
1709
Female
TEN
325
08/21/95
SBU
469
1513
Female
TEN
325
08/21/95
SBU
446
1358
Male
TEN
325
08/23/95
SBU
370
1190
Female
TEN
325
08/23/95
SBU
348
624
Male
TEN
325
08/23/95
SBU
450
1302
Female
TEN
325
08/23/95
SBU
454
1525
Male
TEN
325
08/23/95
SBU
472
1460
Female
TEN
325
08/28/95
SBU
569
2648
Female
TEN
325
08/28/95
SBU
442
1410
Female
TEN
325
08/30/95
SBU
556
2460
Female
TEN
325
08/30/95
SBU
476
1656
Female
IEM
325
08/30/95
SBU
465
1404
Male
325
08/30/95
SBU
450
1272
Male
TEN
325
08/28/95
SBU*
569
2648
Female
-------
Table A-5. Specific Information About Each Fish Collected During 1995 for Long
Term Fish Tissue Study
For Calendar Year : 1995
;tion Site
Date
Species
Length(mm)
Weight(g)
Sex
JACK
TEN
425
10/18/95
CHC
519
1646
Male
TEN
425
10/18/95
CHC
570
1688
Male
TEN
425
10/19/95
CHC
555
1949
Male
TEN
425
10/19/95
CHC
548
1966
Male
TEN
425
11/13/95
CHC
590
2294
Male
TEN
457
10/23/95
CHC
575
2100
Female
TEN
457
10/23/95
CHC
577
2090
Male
TEN
457
10/23/95
CHC
573
1797
Female
TEN
457
10/23/95
CHC
506
1315
Male
TEN
457
10/23/95
CHC
548
1755
Male
TELLICO
LTE
1.0
11/06/95
CHC
598
2684
Female
LTE
1.0
11/06/95
CHC
498
1018
Female
LTE
1.0
11/06/95
CHC
558
1263
Male
LTE
1.0
11/06/95
CHC
470
1007
Male
LTE
1.0
11/06/95
CHC
490
1083
Female
15.0
11/07/95
CHC
458
807
Male
15.0
11/07/95
CHC
532
1269
Female
LTE
15. 0
11/08/95
CHC
410
502
Female
LTE
15.0
11/08/95
CHC
429
526
Male
WATTS
BAR
TEN
531
10/31/95
CHC
506
987
Male
TEN
531
09/12/95
CHC
430
646
Female
TEN
531
10/31/95
CHC
595
2186
Female
TEN
531
09/12/95
CHC
373
437
Male
TEN
531
10/31/95
CHC
600
2044
Female
TEN
560
11/09/95
CHC
495
968
Male
TEN
560
11/09/95
CHC
480
800
Female
TEN
560
11/08/95
CHC
521
1021
Female
TEN
560
11/09/95
CHC
461
837
Female
TEN
600
11/08/95
CHC
570
2047
Male
TEN
600
11/08/95
CHC
420
626
Male
TEN
600
11/09/95
CHC
496
1355
Female
TEN
600
11/09/95
CHC
474
971
Female
600
11/09/95
CHC
511
1257
Male
-------
Appendix B
Recommendations for Fish Tissue Studies in 1996
-------
Study Type/Location
Appendix B. Recommendations for fish tissue studies in 1996*
River Mile Species # Needed Ind/Comp Analvtes
Reservoir Screening
Pickwick Res. TRM 207
TRM 230
TRM 259
BCRM 8
Wilson Res TRM 260
TRM 272
Guntersville Res TRM 350
TRM 375
TRM 423
Watts Bar Res TRM 531
TRM 560
TRM 600
CRM 22
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
-------
Appendix B, Continued
Study Type/Location River Mile Species # Needed Ind/Comp Analvtes
Reservoir Screening, cont.'
Melton Hill Res
CRM 24
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
CRM 45
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
CRM 64
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
So. Holston. Res
SFHRM 51
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
SFHRM 62
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
Watagua. Res
WRM 37
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
WRM 45
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
Fontana Res
LTRM 62
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
LTRM 81
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
TuRM 3
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
Hiwassee Res
HiRM 77
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
HiRM 85
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
-------
Study Type/Location River Mile Species
Reservoir Screening, cont.'
Chatuge Res HiRM 122 CHC
LMB
ShoCrM 1.5 CHC
LMB
Parksville Res ORM 12 CHC
LMB
Bear Creek Res BCM 75 CHC
LMB
L' Bear Cr. Res LBCM 12 CHC
LMB
Cedar Creek Res CCM 25 CHC
LMB
Stream Screenin£
Clarks River CIRM 10 CHC
LMB
Duck River DRM 26 CHC
LMB
Buffalo River BuRM 18 CHC
SMB
Bear Creek
BCM 27
CHC
LMB
Appendix B, Continued
# Needed Ind/Comp Analvtes
5 Composite
5 Composite
5 Composite
5 Composite
5 Composite
5 Composite
5 Composite
5 Composite
5 Composite
5 Composite
5 Composite
5 Composite
Screening - Metals and Organics
Mercury only
Screening - Metals and Organics
Mercury only
Screening - Metals and Organics
Mercury only
Screening - Metals and Organics
Mercury only
Screening - Metals and Organics
Mercury only
Screening - Metals and Organics
Mercury only
5 Composite Screening - Metals and Organics
5 Composite Mercury only
5 Composite Screening - Metals and Organics
5 Composite Mercury only
5 Composite Screening - Metals and Organics
5 Composite Mercury only
5 Composite Screening - Metals and Organics
5 Composite Mercury only
-------
Appendix B, Continued
Study Type/Location River Mile Species # Needed Ind/Comp Analvtes
Stream Screening, cont.'
L'Tenn River
LTRM 95
CHC
5
Composite
Screening - Metals and Organics
SMB
5
Composite
Mercury only
Tuckasegee River
TuRM 10
CHC
5
Composite
Screening - Metals and Organics
SMB
5
Composite
Mercury only
French Br. River
FBRM 77
CHC
5
Composite
Screening Metals and Organics
LMB
5
Composite
Mercury only
Nolichucky River
NolRM 10
CHC
5
Composite
Screening - Metals and Organics
SMB
5
Composite
Screening - Mercury only
Pigeon River
PiRM 7
CHC
5
Composite
Screening - Metals and Organics
SPB
5
Composite
Mercury only
Targeted Screening — None Planned for 1996
Intensive Study — None Planned for 1996
-------
Appendix B, Continued
Study Type/Location River Mile Species # Needed Ind/Comp Analvtes
Long-Term Monitoring
Fort Loudoun Res
TRM 624
CHC
10
Ind
PCBs, DDTr, and Chlordane
Watts Bar Res
TRM 531
STB
5
Composite
PCBs, DDTr, Chlordane
TRM 560
STB
5
Composite
PCBs, DDTr, Chlordane
TRM 600
STB
5
Composite
PCBs, DDTr, Chlordane
CRM 22
STB
5
Composite
PCBs, DDTr, Chlordane
Parksville Res
ORM 16
CHC
5
Comp.
PCBs, DDTr, and Chlordane
a. Note: These recommendations were not final at the time this document was prepared.
-------
Appendix C
New Release from the Alabama Department of Public Health
Revising Fish Consumption Advisories
April 24. 1996
-------
0S/15/'96 15;08 PLftN KtS OhO -» oii Vii rex:
NEWS RELEASE department of public health
4J4 Monroe Street. Montgomery. Alabanui "ft 130-3017 • (334* 61.V5300 • FAX (3?4) 24fM(W7
ADPH revises fish consumption advisories
FOR IMMEDIATE RELEASE CONTACT: Brian Hughes, PhJD.
(334)613-5347
The Alabama Department of Public Health announces it has lifted its fish consumption
advisories for the Tennessee River, but it has added new fisb consumption advisories for the Fish
River in Baldwin County, Logan-Martin Lake and Choccolocco Creek.
Advisories are issued because toxic chemicals in lakes or rivers accumulate in fish tissue.
The people who eat these fish may face health risks. These advisories are updated based on the
results of fish tissue monitoring conducted by the Alabama Department of Environmental
Management and the Tennessee Valley Authority.
Previous advisories to avoid or restrict consumption of fish taken from the Tennessee
River have been removed. These recommendations are based on steadily decreasing DDT
concentrations which fall below the Food and Drug Administration action level of five parts per
million of DDT in fish.
New advisories are as follows:
Fish River: The public is advised not to eat largemouth bass taken from the Fisb River in
Baldwin County because mercury levels have been found to exceed the FDA action level of 1 par
per million. Mercury levels found in fish samples from the Fish River do not cause immediate
health effects; however, at high levels mercury has beer, known to damage the nervous system and
kidneys.
Choccolocco Creek: The department recommends that people not eat tlsh taken from
Choccolocco Creek. This advisory now extends from the point where Hillabee Creek and
Choccolocco Creek meet in Calhoun County downstream to Logan Martin Lake.
This action is based on the results of largemouth bass and channel catfish sampling on
Choccolocco Creek 2.5 miles east southeast of Oxford. The fish in this area were found to have
PCB levels above the Food and Drug Administration's recommended level of 2 parts per million.
(more)
-------
r"i_nfN kc3 xv Oi3 Oi rc«*o
Fish advisories
Add one
Logan Martin Lake: Another fish consumption advisory is being issued for Logan
Martin Lake. The public is advised not to eat largemouth bass, spotted bass and catfish from the
lake.
The department recommends that fish not be eaten from Logan Martin Lake because
largemouth bass, spotted bass and catfish were found to contain levels of PCBs exceeding the
FDA recommended level The department recommends that these three species should not be
consumed from aD area near Riverside, Ala., in St. Clair County downstream to the dam.
PCBs are listed as possible cancer-causing agents in humans. When tested in levels greatly
exceeding those typically found in the environment, PCBs have been associated with the following
health effects:
• a skin disorder known as chloracne,
• changes in cholesterol and triglyceride levels in the blood, and
• tumors in certain rodents.
Advisories are made based on samples which were taken as a part of a five-year fish
program in which samples are analyzed annually. The Alabama Department of Environmental
Management will provide additional testing this fail in the Coosa and Fish River areas. Current
fish consumption advisories are listed here:
BODY OF WATER
PORTION
Between Logan Martin Dam
and Riverside
TYPE OF ADVISORY
Coosa River
Do not consume largemouth
and spotted bass
and all species of
catfish**
Coosa River
Between Riverside
& Alabama-Georgia state line
Limited consumption of
catfish over 1 pound*
Huntsville Spring
Branch & Indian Creek
From Redstone Arsenal to
the Tennessee River
Do not consume channel
catfish, smallmouth
buffalo, brown bullhead,
bigmouth buffalo, white
bass**
(more)
-------
rLHN LIEV - OiJ Oi (OHC
Fish advisories .
Add two
BODY OF WATER
West Point Lake to
Lake Harding
Cold Creek Swamp
Tombigbee River
Choccoiocco Creek
Fish River
PORTION
West Point Lake, Lake Harding
& the intervening stretch of the
Chattahoochee River
10 miles south of the confluence
of the Tombigbee River &
Alabama River adjacent to
the Mobile River
Oiin Basin at river mile 60.5
Between the confluence of Hillabee
Creek and Choccoiocco Creek south
of Oxford, downstream to where
Choccoiocco Creek flows into
Logan Martin Lake
TYPE OF ADVISORY
Do not consume catfish**
Do not consume any fish*"
Do not consume
largemouth bass,
channel catfish**
Do not consume any fish**
Do not consume largemouth
bass
* A limited consumption advisory states that women of reproductive age and children less than 15
years old should avoid eating certain fish from these areas. Other people should limit their
consumption of the particular species to one meal per month.
** Everyone should avoid eating the species of fish listed in the defined area
-30-
4/24/9 6
-------
Appendix D
Species and River Abbreviations Used
in Tables and Appendices
-------
Appendix D. Species and River Abbreviations Used in Tables and Appendicies.
Abbreviations for Species
CHC — Channel catfish
LMB -- Largemouth bass
SBU — Smallmouth buffalo
SMB ~ Smallmouth bass
SPB — Spotted bass
STB -- Striped bass
Abbreviations for Rivers and Creeks
BEC — Bear Creek
BEE — Beech River
BLU - Big Sandy River
BUF — Buffalo River
CLA - Clarks River
DUC — Duck River
ELK —Elk River
HTW — Hiwassee River
HOL -- Holston River
LTE ~ Little Tennessee River
NFH — North Fork Holston River
OCO -- Ocoee River
PIG -- Pigeon River
SEQ — Sequatchie River
TEN -- Tennessee River Mile
TUC - Tuckasegee River
Abbreviations with River Miles
BCM — Bear Creek Mile
BCRM — Bear Creek River (Creek) Mile
BSRM ~ Big Sandy River Mile
BuRM — Buffalo River Mile
CCM -- Cedar Creek Mile
C1RM — Clarks River Mile
CRM ~ Clinch River Mile
DRM — Duck River Mile
ERM — Elk River Mile
FBRM — French Broad River Mile
HiRM — Hiwassee River Mile
HRM — Holston River Mile
LB CM — Little Bear Creek Mile
LTRM — Little Tennessee River Mile
NolRM -- Nolichucky River Mile
ORM -- Ocoee River Mile
PiRM — Pigeon River Mile
ShoCrM ~ Shooting Creek Mile
TRM -- Tennessee River Mile
TuRM -- Tuckasegee River Mile
-------
Results from TVA Fish Tissue Studies on Fish Collected Autumn 1994
and Recommendations for Studies in 1995
By: Don L. Dycus
TVA Water Management
June 1995
Introduction/Backeround
The attached tables summarize results of TVA's fish tissue studies conducted in autumn
1994. These tables and this cover text constitute TVA's report on these results.
TVA's approach to fish tissue contaminant examination is to first conduct screening
studies in which composited samples of an indicator species, such as channel catfish for organics
and largemouth bass for mercury, are examined for a broad array of analytes. Results from
screening studies are used to provide direction for future action. If screening finds low
contaminant concentrations, the site or reservoir would be resampled at the screening level on a
rotational basis in 3 to 5 years. If one or more analytes had somewhat elevated concentrations,
that site would be resampled the next year and samples analyzed for the analyte(s) of concern in a
targeted screening study. If concentrations in screening efforts or targeted screening efforts were
sufficiently high to pose potential human health concerns, the site or reservoir would need to be
examined in an intensive study aimed at determining the species affected, the geographical
distribution, and year-to-year variation. Analysis of individual fish (generally 10 replicates) of
important species from several locations provide the data base for statistical examinations. The
assessment phase would continue until the contaminant concentration was low enough to no
longer be a concern or when year-to-year studies indicated no trend through time. If the former
were the case, the site or reservoir would return to the rotational system. If the latter were the
case, a long-term monitoring study, with either annual or rotational collections (whichever is
appropriate), would be undertaken. The idea for long-term monitoring is to track the problem
analyte so that when concentrations drop below the level of concern a follow-up intensive study
can be conducted to document the problem no longer exists. Generally, composites of indicator
species are analyzed in the contaminant of concern in long-term monitoring studies.
-------
Methods
Details of TV A's collection, processing, and analysis procedures are described in the
report on 1993 fish tissue studies -- "Tennessee Valley Reservoir and Stream Quality - 1993; Fish
Tissue Studies in the Tennessee Valley in 1993" by D.L. Williams and D.L. Dycus. The report
was published in July 1994 and is available from:
Water Management Library
Tennessee Valley Authority
1101 Market Street, CST 16B
Chattanooga, TN 37402-2810
(615) 751-7338 or FAX: (615) 751-7479
One noteworthy change for samples collected for 1994 fish tissue studies is that in
addition to the typical list of organochlorine pesticides analyzed, organophosphate and
chlorophenoxy pesticides were analyzed as recommended by the U.S. EPA in their "Guidance for
Assessing Chemical Contaminant Data for Use in Fish Advisories; Volume 1 Fish Sampling and
Analysis" (EPA 823-R-93-002, August 1993). These include
New organochlorine pesticides: dicofol
Organophosphate pesticides: chlorpyrifos, diazinon, disulfoton, ethion, terbufos, and
carbophenothion
Chlorophenoxy pesticides: oxyfluorfen
Summary of Results
Results from the various fish tissue studies conducted in 1994 are summarized in
Tables 1 - Table 11. Physical information such as length and weight for each fish is in Appendix
A, Tables 1 - 6. Details of study results are available on STORET.
In general, 1994 results were similar to previous years. The most common contaminant of
concern was PCBs. Locations (regardless of study type) with PCB concentrations >0.5 |i/g are
listed in Table 1. Given the increasing interest in mercury, locations (regardless of study type)
with total mercury >0.40 \\Jg are listed in Table 2.
Boxes on the following pages summarize, by study type, locations examined in 1994,
highlights of results, and recommendations for fish tissue studies in 1995. Recommendations for
fish tissue studies in 1995 are listed in Appendix B. (Note: These recommendations were not final
at the time this document was prepared.)
-------
Screening Studies
Reservoirs: Results in Table 3 and Appendix Table A-l.
Reservoirs sampled in Autumn 1994: Beech and Douglas.
Results highlights: None of the analytes in either reservoir were sufficiently high to be
noteworthy.
Recommendations: Neither of these reservoirs need to be resampled until they come up
again in the standard 3-year rotation. Several reservoirs have not been sampled
recently and need to be included in the rotation in 1995. However, routine fish
community studies, which usually provide most of the fish for analysis, will not be
conducted on all of these reservoirs in 1995 so they will not be sampled until 1996.
Reservoirs to be sampled in 1995 include: Kentucky, Normandy, Beech,
Tims Ford, Chickamauga, Fort Loudoun, and Fort Patrick Henry.
Rivers: Results in Table 4 and Appendix Table A-2.
Rivers sampled in summer 1994: Clarks, Duck, Buffalo, Elk, Hiwassee, Ocoee,
Little Tennessee, Tuckasegee, French Broad, Nolichucky, Pigeon, North
Fork Holston.
Results highlights: None of the organochlorine pesticides or PCBs were high enough to
be noteworthy. Only one sample contained detectable levels of one of new
pesticides examined for the first time on 1994 fish (see methods). The channel
catfish sample from Hiwassee River Mile 38 contained 0.05(i/g of ethion. None of
the other samples, regardless of location or study, had detectable levels of any of
these pesticides. Mercury was the only metal found in sufficiently concentrations
to be of interest. Sample locations with mercury concentrations >0.4(o/g are listed
in Table 2.
Recommendations: Six of the river screening sites were sampled for the first time in 1994.
These (Clarks, Buffalo, Ocoee, Tuckasegee, Pigeon, and North Fork Holston)
should be resampled in summer 1995. Fish tissue samples have never been
collected from Bear Creek, so that site should be sampled in 1995. Two other
sites (Sequatchie and Holston) were not sampled in 1994 and should be in 1995 to
take advantage of fish communities studies planned for those sites.
-------
Targeted Screening Studies
Reservoirs: Results in Table 5 and Appendix Table A-3.
Reservoirs sampled in Autumn 1994, including analytes and species of concern:
Wheeler (PCBs - channel catfish)
Chickamauga (inflow only, PCBs - channel catfish)
Parksville (PCBs - channel catfish)
Tellico (mercury - largemouth bass)
Cherokee (PCBs - channel catfish).
Results highlights: PCB concentrations were near or above 1.0 jo/g in the reservoirs listed
above. This is sufficiently high to repeated targeted screening in 1995, but not so
high as to warrant intensive investigations. Mercury concentrations in Tellico
largemouth bass were relatively low, indicating no need for further sampling in
1995. None of the screening studies conducted in 1994 indicated a need for
Targeted Screening studies in 1995.
Recommendations: Targeted screening studies will be conducted on the following
reservoirs in 1995: Wheeler (PCBs - channel catfish), Cherokee (PCBs - channel
catfish and striped bass/hybrids), Nickajack (PCBs - channel catfish and striped
bass/hybrids, Parksville (PCBs - channel catfish). Targeted screening samples
will not be conducted on Chickamauga in 1995 because channel catfish from that
reservoir will examined in Reservoir Screening studies, which include a broad list
of analytes including PCBs.
Rivers: None sampled for Targeted Screening in 1994; none needed in 1995.
-------
Intensive Studies
Reservoirs: Results in Table 6, 7, and 8 and Appendix Table A-4.
Reservoirs sampled in 1994, including analytes and species of concern: Nickajack (PCBs -
striped bass).
Results highlights: The average of the 10 striped bass collected from TRM 469 in autumn
1995 was 1.2|i/g and the range was 0.7 to 2.1 jx/g. In 1992 the mean was 0.8|i/g
and in 1993 1.0(i/g. Striped bass collected for analysis in 1994 were larger than in
the previous years (mean weights were 2305g in 1992, 4360g in 1993, and 7987g
in 1994. Preliminary examination for covariance analysis indicated a relationship
between PCB concentrations and fish weights (but not lipid content), hence
adjustment of PCB concentrations for fish weights was necessary for statistical
comparisons among years. Adjusted PCB concentrations were not significantly
different among years at a = 0.05.
Recommendations: These results were provided to the Tennessee Department of
Environment and Conservation for evaluation of potential human health
implications. TDEC has advised pregnant women, nursing mothers, and children
should not eat channel catfish from Nickajack, others should limit consumption to
1.2 pounds per month. Given the consistency in PCB concentrations for the past
three years, striped bass from Nickajack will not be sampled for an Intensive Study
in 1995, rather they will be sampled as part of a Targeted Screening study in 1995.
This means a 5-fish composite will be collected from TRM 469-470 and analyzed
for selected organics including PCBs. Channel catfish will also be collected for
that study.
Rivers: None sampled for Intensive Studies in 1994; none needed in 1995.
-------
Long-Term Monitoring Studies
Reservoirs: Results in Table 9, 10, and 11 and Appendix Tables A-5 and A-6.
Reservoirs sampled in autumn 1994, including analytes and species of concern:
Nickajack (PCBs - channel catfish)
Watts Bar (PCBs - channel catfish and smallmouth buffalo)
Fort Loudoun (PCBs - channel catfish)
Tellico (PCBs - channel catfish).
Results Highlights: TDEC has issued fish consumption advisories on all these reservoirs
due to PCB contamination. They have all been examined intensively during past
years and are now the long-term monitoring phase. Nickajack is the only reservoir
which has exhibited a decrease in PCB concentrations. Table 8 summarizes PCB
concentrations in various species over the past seven years. Mean concentrations
in channel catfish taken from near Nickajack Dam (TRM 425) for the period 1988
- 1994 have been 0.9, 1.3, 1.0, 1.5, 0.4, 0.6, and 0.7|x/g, respectively and at TRM
457 for the same period 1.3, 0.7, 1.1, 0.9, 0.5, 0.7, and 0.7|o/g, respectively.
(Note: data for all years except 1994 are means from fish analyzed individually;
whereas, one, 5-fish composite was analyzed from each location in 1994.)
PCB concentrations in channel catfish from Watts Bar, Fort Loudoun, and
Tellico have varied from year to year but no trend (either increasing or decreasing)
is evident. PCB concentrations in catfish from these three reservoirs in 1994 were
within the range of concentrations observed in past studies; again indicating no
trend.
Analyses were based on 5-fish composites for all reservoirs except Fort
Loudoun where 9 individual catfish were analyzed from the long-term, trend site at
TRM 624. Individuals were examined from this site because it is has been
monitored longer than any other TVA site with all previous years based on analysis
of individual samples. PCB concentration each fish is shown in Table 10 along
with other important results. Concentrations averaged 1.6|i/g with a range of 0.6
to 3.1|i/g in 1994. Table 11 compares 1994 results to previous year; mean
concentrations from 1985 and 1986 to 1994 were 1.4, 1.5, 1.2, 2.3, 1.0, 2.5, 1.8,
1.2, and 1.6, respectively. Fish weights, an important variable in fish tissue studies,
have varied among years. Preliminary examination for covariance analysis
identified a relationship between fish weight and PCB concentration but not for
lipid content, another important variable. Covariance analysis found a significant
difference in adjusted PCB concentrations among years but there was no pattern or
trend.
Recommendations: Given that fish consumption advisories have been issued for these
reservoirs, these studies will be repeated in 1995.
Rivers: None sampled for Long-Term Monitoring Studies in 1994; none needed in 1995.
-------
Table 1. Highlights of Autumn 1994 Results from Areas with Advisories and/or
"High" (i.e., >0.5 jj.g/g) PCB Concentrations. All Samples Analyzed as
5-Fish Unless Otherwise Noted
Location Species PCBs DDTr Chlordane
Wheeler Reservoir
TRM277
CHC
0.8
1.0
0.02
TRM296
CHC
1.0
0.8
0.02
TRM347
CHC
1.3
0.55
0.03
Nickajack Reservoir
TRM425
CHC
0.7
0.08
0.03
TRM457
CHC
0.7
0.07
0.02
STB'
1.2
0.23
0.07
Chick. Reservoir
TRM529
CHC
1.0
0.10
0.04
Watts Bar Reservoir
TRM530
CHC
1.0
0.12
0.06
SMB
0.6
0.07
0.02
TRM560
CHC
1.0
0.12
0.05
SMB
0.4
0.05
0.02
TRM600
CHC
1.0
0.16
<0.01
Ft. Loudoun Res.
TRM624
CHCb
1.6
0.10
0.06
Tellico Reservoir
LTRM 1
CHC
2.3
0.26
0.10
LTRM 15
CHC
1.1
0.18
0.04
Ocoee Reservoir #3
ORM 12
CHC
1.2
0.04
0.01
CHC
1.7
0.05
<0.01
Cherokee Reservoir
HRM53
CHC
0.9
0.04
0.04
HRM76
CHC
0.8
0.02
0.04
a. Average of 10 striped bass analyzed individually
b. Average of 9 channel catfish analyzed individually
-------
Table 2. Highlights of Autumn 1994 Results from Areas with "Elevated" (i.e.,
>0.40 ng/g) Total Mercury Concentrations. For Largemouth (LMB),
Smallmouth (SMB), and Spotted (SPB) Bass, Analysis Conducted on Largest
of Five Individuals Collected from a Site. For Channel Catfish (CHC),
Analysis conducted on 5 Composited Individuals
Weight Mercury
Location Species (gm. if individual) (Total, ug/g)
Clarks River Mile 9
LMB
1434
0.57
Duck River Mile 22
LMB
1670
0.50
Buffalo River Mile 17
SMB
708
0.52
Elk River Mile 41
SPB
548
0.48
Hiwassee River Mile 38
LMB
964
0.58
Ocoee River Mile 2
LMB
996
0.91
Little Tenn. River Mile 94
SMB
415
0.60
Tuckasegee River Mile 15
SMB
410
0.63
French Broad River Mile 78
SMB
1474
0.82
N. Fork Hoi. River Mile 4
CHC
Composite
0.74
Note: Additional bass samples were collected from the Nolichucky (SPB), Pigeon (SPB), and
North Fork Holston (SMB) rivers; all had concentrations < 0.40 \xsjg. Additional mercury data
are in the following tables.
-------
Table 3. Concentrations (ug/g) of organics and metals in composited fish samples from reservoir screening locations collected in autumn
1994
Reservoir/River
Orgaiiochloriiie Pesticides and PCBs
Species Lipid Mirex Toxa Hepta Aldrin Benz DDTr Dield Endosu Endri Chlor PCBs Dicofol
Beech Reservoir
BeeRM 36
Douglas Reservoir
FBRM33
FBRM51
CHC 7.8 <0.008 <0.5 <0.01 <0.01 <0.01 0.32 <0.01 <0.01 <0.01 <0.01 <0.1 <0.01
CHC 4.0 <0.008 <0.5 <0.01 <0.01 <0.01 0.11 <0.01 <0.01 <0.01 0.04 0.2 <0.01
CHC 7.8 <0.008 <0.5 <0.01 <0.01 <0.01 0.11 <0.01 <0.01 <0.01 0.05 0.2 <0.01
Reservoir/River
Organ op host) hate and Chloronhenoxy Pesticides
Species Lipid Chlorpyrif Diazinon Disulfoton Ethioin Terbufos Carbophen Oxvfluor
Beech Reservoir
BeeRM 10
Douglas Reservoir
FBRM33
FBRM51
CHC 7.8
CHC
CHC
4.0
7.8
<0.01 <0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01 <0.01 <0.01 <0.5
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.5
<0.5
Metals
Reservoir/River
Species
Arsenic
Cadmium
Lead
Mercury
Selenium
Beech Reservoir
BeeRM 10
Douglas Reservoir
FBRM33
FBRM51
CHC
LMB
CHC
CHC
<0.10
<0.10
<0.10
<0.05
<0.05
0.05
<0.02
<0.02
0.04
0.14
0.25
0.26
0.18
<0.2
<0.2
<0.2
-------
Table 4. Concentrations of organics and metals in composited fish samples from stream screening locations in summer 1994
River
Organoclilorine Pesticides and PCBs
Mile Spec Lipid Mircx Toxa Hepta Aldri BenzHe DDTr Dieldr Endosu Endri Chlor PCBs
Dicofol
Buffalo R 18 CHC 3.9 <0.008 <0.5 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 0.4 <0.01
ClarksR 10 CHC 9.8 <0.008 <0.5 <0.01 <0.01 <0.01 0.02 0.04 <0.01 <0.01 0.02 0.1 <0.01
Duck R 22 CHC 4.7 <0.008 <0.5 <0.01 <0.01 <0.01 0.05 0.01 <0.01 <0.01 <0.01 0.1 <0.01
Elk R 41 CHC 5.8 <0.008 <0.5 <0.01 <0.01 <0.01 0.36 <0.01 <0.01 <0.01 <0.01 <0.1 <0.01
French Broad R 78 CHC 4.8 <0.008 <0.5 <0.01 <0.01 <0.01 0.03 <0.01 <0.01 <0.01 0.01 <0.1 <0.01
Hiwassee R 38 CHC 9.1 <0.008 <0.5 <0.01 <0.01 <0.01 0.03 <0.01 <0.01 <0.01 0.01 0.2 <0.01
Liltle Tennessee R 94 CHC 6.8 <0.008 <0.5 <0.01 <0.01 <0.01 0.04 <0.01 <0.01 <0.01 0.02 0.1 <0.01
N. Fk. Holston R 4 CHC 9.5 <0.008 <0.5 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 0.3 <0.01
Nolichucky R 8 C 6.9 <0.008 <0.5 <0.01 <0.01 <0.01 0.04 <0.01 <0.01 <0.01 <0.01 <0.1 <0.01
OcoeeR 3 CHC 3.3 <0.008 <0.5 <0.01 <0.01 <0.01 0.02 <0.01 <0.01 <0.01 0.01 0.2 <0.01
Pigeon R 8 CHC 3.1 <0.008 <0.5 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.1 <0.01
TuckasegeeR 15 CHC 9.5 <0.008 <0.5 <0.01 <0.01 <0.01 0.04 <0.01 <0.01 <0.01 0.01 <0.1 <0.01
River
Mile
Species
Organophosphate and Chloronhenoxy Pesticides
Lipid Clilorovrif Diazinon Disulfoton Ethion
Terbufos Carbophen Oxvflnor
Buffalo
Clarks R
Duck R
18
10
22
CHC
CHC
CHC
3.9
9.8
4.7
<0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.5
<0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.5
<0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.5
-------
Table 4. Continued
River
Mile
Organophosnhate and Chloronheiioxv Pesticides. Cont'
Species Lipid Dursban Diazinon Disulfoton Elhion Terbufos
Carbophen Oxvfluor
Elk R ,41
French Broad R 78
Hiwassee R 38
Little Tennessee R 94
N. Fk. Holston R 4
Nolichucky R 8
Ocoee R 3
Pigeon R 8
TuckasegeeR 15
CHC
CHC
CHC
CHC
CHC
C
CHC
CHC
CHC
5.8
4.8
9.1
6.8
9.5
6.9
3.3
3.1
9.5
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
0.05
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.5
<0.5
<0.5
<0.5
<0.5
<0.5
<0.5
<0.5
<0.5
River
Mile
Species
Arsenic
Metals
Cadmium Lead
Mercury
Selenium
Buffalo R
Clarks R
Duck R
Elk R
18
10
22
41
CHC
SMB
CHC
LMB
CHC
LMB
CHC
SPB
<0.10
<0.10
<0.10
<0.10
<0.05
<0.05
<0.05
<0.05
<0.02
0.03
<0.02
<0.02
0.11
0.52
0.10
0.57
<0.10
0.50
<0.10
0.48
<0.2
<0.2
<0.2
<0.2
-------
Table 4. Continued
River Mile Species Arsenic
French Broad R 78 CHC <0.10
SMB
HiwasseeR 38 CHC <0.10
LMB
Little Tennessee R 94 CHC <0.10
SMB
N. Fk. Holston R 4 CHC <0.10
SMB
NoIichuckyR 8 C <0.10
SPB
Ocoee R 3 CHC <0.10
LMB
Pigeon R 8 CHC <0.10
SPB
Tuckasegee R
15
CHC
SMB
<0.10
Metals. Cont'
Cadmium Lead
Mercury Selenium
<0.05
0.05
<0.10
0.82
<0.2
<0.05
0.02
<0.10
0.58
<0.2
<0.05
<0.02
0.38
0.60
<0.2
<0,05
0.04
0.74
0.31
<0.2
<0.05
0.11
0.20
0.38
<0.2
<0.05
0.05
0.12
0.91
0.2
<0.05
0.04
0.12
0.34
<0.2
<0.05
<0.02
0.19
0.63
<0.2
-------
Table 5. Concentrations (ug/g) of selected organics and metals in composited fish samples from reservoir targeted screening locations
in 1994
Reservoir/River
Species Lipid Mi rex
Selected Orgaiioclilorine Pesticides and PCBs
Toxa Hepta Aldrin Benz DDTr Diel Endosul Endri Chlor PCBs Dicofol
Chickamauga Reservoir -
TRM 529 CHC
13
0.10
0.04
1.0
Cherokee Reservoir
HolRM 53 CHC 4.6
HolRM 76 CHC 6.1
0.04
0.02
0.04
0.04
0.9
0.8
Parksville(Ocoee #1) Reservoir
OcoRM 12 CHC 4.9
OcoRM 16 CHC 7.4
0.04
0.05
0.01
0.01
1.2
1.7
Wheeler Reservoir
TRM 277 CHC 5.6
TRM 296 CHC 9.5
TRM 347 CHC 6.6
1.02
0.80
0.55
0.02
0.02
0.03
0.8
1.0
1.3
Reservoir/River
Metals
Species
Arsenic
Cadmium
Lead
Mercury
Selenium
Tellico Reservoir
LTRM 1
LTRM 15
LMB
LMB
0.13
0.18
Parksville (Ocoee #1) Reservoir
OcoRM 12 CHC
OcoRM 16 CHC
0.4
0.5
-------
able 6. Concentrations of selected pesticides and PCBs in individual fish collected for a reservoir intensive
tudy on Nickajack Reservoir in autumn 1994
Fish Collection Length Weigth Sex Lipid PCBs Chlordane DDTr
Number Date (mm) (gm) (%) (ug/gm) (ug/g) (ug/g)
1
11/18/94
872
8809
female
13
1.1
0.1
0.15
2
11/18/94
774
5179
female
11
0.9
0.08
0.18
3
11/21/94
1010
12500
female
11
1.8
0.1
0.36
4
11/21/94
874
7627
female
9.4
1.2
0.07
0.15
5
11/21/94
776
5590
male
9.1
1.1
0.06
0.2
6
11/21/94
804
7711
female
12
0.7
0.05
0.1
7
11/21/94
791
6330
male
12
1
0.06
0.18
8
11/21/94
937
9895
female
10
2.1
0.11
0.6
9
11/21/94
830
7917
female
11
0.8
0.05
0.15
10
11/21/94
852
8309
female
11
1.3
0.06
0.18
Mean 852 7987 11 1.2 0.07 0.23
-------
T<' . Summary of lengths, total weights, and percent lipids of iel catfish, carp, and striped bass from Nickajack Reservoir,-
collected from 1988 to 1994
Weight Ranee
Mean WeieHt
Leneth Ranee
Mean Leneth
% l.inid Ranee
Mean % Lipid
1988
Catfish'
TRM 425 ,
TRM 457
1835-2705
1 198-2340
2175
1854
555-650
472-602
587
540
0.9-18.0
8.9-20 0
11.4
13.6
1989
Catfish
TRM 425
TRM 457
346-i798
308-1001
1048
805
331-565
332-470
458
397
3.0-20.0
3 2-17.0
10.3
10.9
1990
Catfish
TRM 425
TRM 457
464-2332
736-2429
1215
1500
370-596
426-656
484
528
5.4-20.0
3.6-24.0
10.7
12.4
1991
Catfish
TRM 425
TRM 457
570-2512
962-2839
1607
2100
395-597
451-625
521
565
4.8-14.0
0.1-27.0
8.1
14.1
Carp
TRM 425
TRM 457
1602-5017
3522-7932
3350
4958
477-725
633-780
617
686
4.0-16.0
3.9-14.0
10.1
9.4
1992
Catfish
TRM 425
TRM 457
762-1845
883-2620
1144
1453
446 -585
463-610
497
516
2.3-12.0
2.3-20.0
7.3
10.1
Carp
TRM 425
TRM 457
3460-8414
3635-8943
5150
6552
633-846
646-799
708
749
2.6-12.0
3.5-12.0
6.2
6.5
Striped Bass
TRM 470
1619-3311
2305
494-686
594
73-12.0
9.1
-------
T Continued
Weight Ranee
Mean Weight
length Range
Mean Length
% Linid Range
Mean % Lipid
1993
Catfish
TRM 425
650-2359
1293
422-595
506
1.8-13.0
6.8
TRM 457
663-2141
1259
412-575
488
3.7-14.0
8.1
Carp
6.8
TRM 425
2602-6881
5238
569-760
689
3.5-9.1
TRM 457
3768-6547
4972
655-750
704
2.9-10.0
5.3
Striped Bass
8.3
TRM 469
1618-7324
4360
542-850
712
5.3-13.0
1994
Catfishb
TRM 425
1023-2341
1574
482-591
531
N/A
8.0
TRM 457
975-2790
1755
486-627
557
N/A
15.0
Striped Bass
11.0
TRM 469
5179-12500
7987
776-1010
852
9.1-13.0
a. Collected in January and February 1989
b. Samples analyzed as single, 5-fish composites
-------
T Summary of total PCB concentrations (ng/g) in catfish, c mallmouth buffalo, and striped bass fillets from Nickajack
Reservoir, collected from 1988 to 1994
Catfish
Carp
Sniallmouth Buffalo
Striped Bass
1988
Range
Mean
Number > 2.0jig/g
Number offish
1989
Range
Mean
Number > 2.0ng/g
Number offish
1990
Range
Mean
Number >2.0|ig/g
Number offish
1991
Range
Mean
Number >2.0|jg/g
Number offish
1992
Range
Mean
Number >2.0(ig/g
Number offish
1993
Range
Mean
Number > 2.0ng/g
Number offish
1994
Range
Mean
Number >2.0fig/g
Number of fish
TRM 425
0.4-1.9
0.9
0
10
0.6-2.0
1.3
1
10
0.6-1.5
1.0
0
10
0 3-3.6
1 5
2
10
0.1-0.8
0.4
0
10
0.3-1.0
0.6
0
10
0.7
b
TRM 457
0.9-1.7
1.3
0
3
0.6-2.0
0.7
1
10
0.4-1.7
1.1
0
10
0.2-1.9
0.9
0
10
0.1-0.8
0.5
0
10
0.3-1.2
0.7
0
10
0.7
b
TRM 425
TRM 457
0.1-0.8
0.3
0
10
0.1-0 7
03
0
10
0.2-0.6
0.3
0
10
0.3-2.7
1.2
1
9
0.1-0.6
0.3
0
9
0.4-1.8
0.7
0
10
TRM 425
0 1-0.7
0.2
0
10
TRM 457
0.1-0 7
04
0
4
TRM 470
0.5-1.1
0.8
0
8
0 6-1.9
1.0
0
10
0.7-2.1
1.2
1
10
a. Catfish collected in January and February 1989.
b. One, 5-fish composite analyzed
-------
Tauic 7. Concentrations (ug/g) of selected organochlorine pestic: nd PCBs in composited fish samples for reservoir long-term
monitoring studies in autumn 1994
Reservoir/River Species Lipid Mirex Toxa Hepta Aldrin BenzHe DDTr Dield Endosu Endri Chlor PCBs Dicofol
Tellico Reservoir
LTRM 1 CHC 6.4
LTRM 15 CHC 2.6
0.26
0.18
0.10
0.04
2.3
1.1
Nickajack Reservoir
TRM 425 CHC 8.0
TRM457 CHC 15
0.08
0.07
0.04
0.02
0.7
0.7
Walts Bar Reservoir
TRM 530 CHC 5.5
SBU 11
0.12
0.07
0.06
0.02
1.0
0.6
TRM 560
CHC
SBU
4.6
10
0.12
0.05
0.05
0.02
1.0
0.4
TRM 600
CHC
SBU
2.5
10
0.16
0.10
<0.01
0.16
1.0
0.9
-------
'able 10. Concentrations of selected organochlorine pesticides and PCBs in individual fish samples for reservoir
ang-term monitoring studies on Fort Loudoun Reservoir in autumn 1994
Number Collection Length Weigth Sex Lipid PCBs Chlordane DDTr
Date (mm) (g) (%) (ug/g) (ug/g) (ug/q)
1
10/4/94
480
1166
male
3
3.1
0.04
0.22
2
10/4/94
390
500
male
3.2
2.2
0.09
0.13
3
10/4/94
485
1026
male
5.7
1.6
0.04
0.08
4
10/4/94
385
442
male
2.4
0.9
0.02
0.04
5
10/4/94
662
2676
female
1.6
0.9
0.03
0.06
6
10/5/94
417
538
male
0.7
1.1
0.03
0.07
7
10/5/94
455
822
male
4.1
2.5
0.17
0.17
8
10/5/94
416
515
female
1.7
0.6
0.06
0.06
9
10/5/94
365
425
male
4
1.1
0.03
0.06
Mean
451
901
2.9
1.6
0.06
0.10
-------
Cable 11. Summary of PCB concentrations in channel catfish (the only species sampled in 1994), carp, and
white bass collected from Fort Loudoun Reservoir since 1985; collected in autumn 1994 for
long-term monitoring study
Location
PCB Range
Mean
No>2.0
# Fish
TRM
(ue/e)
(ueJz)
(ug/el
Catfish
1985
628
0.2-2.8
1.4
2
10
1987
628
0.1-4.5
1.5
2
10
1988
628
0.2-4.4
1.2
1
10
1989
628
0.6-4.3
2.3
11
20
1990
628
0.3-1.9
1.0
0
10
1991
624
1.4-4.6
2.5
7
10
1992
624
0.1-4.2
1.8
3
9
1993
624
0.4-2.2
1.2
2
10
1994
624
0.6-3.1
1.6
3
9
Carp
1992
651
0.2-0.9
0.6
0
10
White Bass
1987a
628
b
<0.1
a
5
640
b
<0.1
a
5
1992
651
0.3-1.2
0.5
0
10
a. Catfish were sampled from TRMs 624-629. White bass and carp were collected from TRM 651 in 1992.
b. Five white bass were collected from TRMs 628 and 640 in 1987. Each set of five was analyzed as a composite sample.
-------
Appendix A
Specific physical information on all fish collected
for fish tissue sstudies in 1995
-------
Table A-l
Specific physical information on composite fish collected for tissue
Gtroam and - reservoir locations as part of screening studies.
-O
3E
'on Site
J
-------
Table A-2-
Specific physical information on composite fish collected for tissue
stream and rooorvoir locations as part of screening studies.
2c" "ion Site Date Species Length (mm) Weight (g) Sex LABID
3L RIVER
BUFFALO R
17.7
07/13/94
CHC
386
602
Female
BUFFALO R
17 .7
07/13/94
CHC
444
754
Male
BUFFALO R
17.7
07/13/94
CHC
458
962
Male
BUFFALO R
17.7
07/13/94
CHC
379
524
Female
BUFFALO R
17.7
07/13/94
CHC
392
484
Female
BUFFALO R
17.7
07/13/94
SMB
378
708
Female
BUFFALO R
17.7
07/13/94
SMB
245
178
Male
BUFFALO R
17 .7
07/13/94
SMB
258
208
Male
BUFFALO R
17.7
07/13/94
SMB
264
218
Female
COWER TENNESSE R
CLARKS
R
9.8
07/14/94
CHC
546
2230
Female
CLARKS
R
9.8
07/14/94
CHC
399
586
Female
CLARKS
R
9.8
07/14/94
CHC
418
718
Female
CLARKS
R
9.8
07/14/94
CHC
413
694
Female
CLARKS
R
9.8
07/14/94
LMB
414
1202
Female
CLARKS
R
9.8
07/14/94
LMB
366
882
Male
CLARKS
R
9.8
07/14/94
LMB
430
1434
Female
CLARKS
R
9.8
07/14/94
LMB
356
724
Female
CLARKS
R
9.8
07/14/94
LMB
390
1004
Female
1 5
R
9.8
07/14/94
LMB
0
0
Female
DU ^ER
DUCK RIVER
22.5
07/12/94
CHC
389
460
Male
DUCK RIVER
22.5
07/12/94
CHC
404
604
Male
DUCK RIVER
22.5
07/12/94
CHC
375
504
Male
DUCK RIVER
22.5
07/12/94
CHC
351
390
Female
DUCK RIVER
22.5
07/12/94
CHC
352
392
Male
DUCK RIVER
22.5
07/12/94
LMB
4 67
1670
Female
DUCK RIVER
22.5
07/12/94
LMB
471
1534
Female
SLK RIVER
ELK R
(TRIB. TO
05/10/94
CHC
458
958
Male
ELK R
(TRIB. TO
05/10/94
CHC
443
892
Male
ELK R
(TRIB. TO
05/10/94
CHC
417
652
Male
ELK R
(TRIB. TO
05/10/94
CHC
431
778
Male
ELK R
(TRIB. TO
05/10/94
CHC
445
826
Male
ELK R
(TRIB. TO
06/30/94
SPB
233
168
Female
ELK R
(TRIB. TO
06/30/94
SPB
274
545
Male
ELK R
(TRIB. TO
06/30/94
SPB
248
440
Female
ELK R
(TRIB. TO
06/30/94
SPB
235
475
Female
FRENCH BROAD
RIVER
FCFMrH
BROAD R
06/13/94
CHC
420
728
Male
H
BROAD R
06/13/94
CHC
440
696
Male
H
BROAD R
06/13/94
CHC
448
632
Female
FRENCH
BROAD R
06/13/94
CHC
379
404
Male
Page 1
-------
Table A-2.
Specific physical information on composite fish collected for tissue
stream—and reaorvoir locations as part of screening studies.
Ccn" "ion Site
Date
Species
Length(mm)
Weight(g)
Sex
I BROAD R
06/16/94
CHC
314
262
Male
FRENCH BROAD R
06/17/94
CHC
500
1016
Female
FRENCH BROAD R
06/01/94
SMB
260
280
Male
FRENCH BROAD R
06/01/94
SMB
260
214
Male
FRENCH BROAD R
06/09/94
SMB
360
620
Female
FRENCH BROAD R
06/09/94
SMB
460
1502
Female
FRENCH BROAD R
06/16/94
SMB
486
1474
Female
FRENCH BROAD R
06/16/94
SMB
215
114
Female
FRENCH BROAD R
06/16/94
SMB
245
184
Female
FRENCH BROAD R
06/17/94
SMB
230
162
Female
HIWASSEE RIVER
HIWASSEE R 3 8.0
07/05/94
CHC
317
286
Female
HIWASSEE R 38.0
07/06/94
CHC
362
498
Male
HIWASSEE R 38.0
07/07/94
CHC
331
364
Male
HIWASSEE R 38.0
07/07/94
CHC
469
1046
Female
HIWASSEE R 38.0
07/07/94
CHC
455
936
Male
HIWASSEE
HIWASSEE R 38.0
05/04/94
LMB
302
370
Female
HIWASSEE R 38.0
07/05/94
LMB
344
500
Female
HIWASSEE R 38.0
07/06/94
LMB
338
566
Female
SEE R 38.0
07/05/94
LMB
453
964
Female
SEE R 38.0
07/05/94
LMB
375
547
Male
LITTLE TENNESSEE
LITTLE TENNESSEE
R
08/08/94
CHC
540
1674
Female
LITTLE TENNESSEE
R
08/08/94
CHC
350
382
Male
LITTLE TENNESSEE
R
06/20/94
SMB
250
198
Male
LITTLE TENNESSEE
R
06/21/94
SMB
265
220
Male
LITTLE TENNESSEE
R
06/21/94
SMB
305
415
Female
LITTLE TENNESSEE
R
06/21/94
SMB
250
232
Female
LITTLE TENNESSEE
R
06/21/94
SMB
275
256
Male
HOLSTON RIVER
N FK HOLSTON R
05/17/94
CHC
534
1522
Male
N FK HOLSTON R
05/17/94
CHC
495
1232
Female
N FK HOLSTON R
05/17/94
CHC
464
386
Male
N FK HOLSTON R
05/17/94
CHC
453
950
Male
N FK HOLSTON R
05/19/94
CHC
638
3102
Female
N FK HOLSTON R
05/17/94
SMB
371
658
Female
N FK HOLSTON R
05/17/94
SMB
436
1254
Male
N FK HOLSTON R
05/17/94
SMB
341
502
Male
N FK HOLSTON R
05/17/94
SMB
384
842
Female
N—EK HOLSTON R
05/17/94
SMB
364
590
Male
ICKY RIVER
:HUCKY R 8
.5
05/31/94
C
791
8534
Female
LABID
Page 2
-------
Table A-i
Specific physical information on composite fish collected for tissue
stream and reservoir locations as part of screening studies.
~ Lon Site
Date
Species
Length(mm)
Weight(g)
Sex
[UCKY R
8.5
05/31/94
C
622
2984
Male
NOLICHUCKY R
8.5
05/31/94
C
580
2842
Male
NOLICHUCKY R
8.5
05/31/94
C
492
1698
Male
NOLICHUCKY R
8.5
05/31/94
SPB
377
806
Female
NOLICHUCKY R
8.5
05/31/94
SPB
310
438
Female
NOLICHUCKY R
8.5
05/31/94
SPB
291
336
Male
NOLICHUCKY R
8.5
05/31/94
SPB
245
228
Female
NOLICHUCKY R
8.5
05/31/94
SPB
259
240
Female
DCOEE RIVER
OCOEE R 2.5
07/19/94
CHC
382
392
Female
OCOEE R 2.5
07/20/94
CHC
420
688
Female
"OCOEE R 2.5
07/20/94
CHC
501
1024
Female
OCOEE R 2.5
07/20/94
CHC
391
500
Male
OCOEE R 2.5
07/20/94
CHC
391
530
Male
OCOEE R 2.5
07/19/94
LMB
308
316
Female
OCOEE R 2.5
07/20/94
LMB
407
996
Male
OCOEE R 2.5
07/20/94
LMB
334
408
Female
OCOEE R 2.5
07/20/94
LMB
284
274
Male
PIGEON RIVER
PIGEON R 8.2
07/08/94
CHC
558
1935
Female
N R 8.2
07/08/94
CHC
414
585
Male
N R 8.2
07/08/94
CHC
336
380
Female
PIGEON R 8.2
07/08/94
CHC
485
975
Female
PIGEON R 8.2
07/08/94
CHC
464
855
Male
PIGEON R 8.2
07/08/94
SPB
395
840
Female
PIGEON R 8.2
07/08/94
SPB
360
660
Female
PIGEON R 8.2
07/08/94
SPB
300
330
Male
PIGEON R 8.2
07/08/94
SPB
330
500
Female
PIGEON R 8.2
07/08/94
SPB
373
780
Female
TUCKASEGEE RIVER
TUCKASEGEE R
15.0
08/09/94
CHC
464
1034
Female
TUCKASEGEE R
15. 0
08/09/94
CHC
434
664
Female
TUCKASEGEE R
15.0
08/09/94
CHC
405
592
Female
TUCKASEGEE R
15. 0
08/09/94
CHC
376
478
Male
TUCKASEGEE R
15.0
08/09/94
CHC
402
562
Female
TUCKASEGEE R
15.0
08/09/94
SMB
295
332
Male
TUCKASEGEE R
15.0
08/09/94
SMB
250
210
Male
TUCKASEGEE R
15.0
08/09/94
SMB
250
208
Male
TUCKASEGEE R
15.0
08/09/94
SMB
315
410
Female
TUCKASEGEE R
15.0
08/09/94
SMB
295
384
Female
Page 3
-------
Table A-3
Specific physical information on composite fish collected for tissue
atream and reservoir locations as part ofyscreening studies.
Co
I
a.
:ion Site
SE
Date
VccJ
Species Length(mm) Weight(g) Sex
TELLICO
LITTLE TENNESSEE R 10/2 0/94 LMB
LITTLE TENNESSEE R 10/20/94 LMB
LITTLE TENNESSEE R 10/20/94 LMB
LITTLE TENNESSEE R 10/20/94 LMB
LITTLE TENNESSEE R 10/20/94 LMB
LITTLE TENNESSEE R 10/21/94 LMB
LITTLE TENNESSEE R 10/21/94 LMB
E TENNESSEE R 10/21/94 LMB
E TENNESSEE R 10/21/94 LMB
PARKSVTLLE - OCOEE N
317
503
447
392
376
530
336
350
336
454
1954
1178
844
720
2650
460
518
340
LABID
HOLSTON
R
53.0
09/08/94
CHC
572
1902
Female
HOLSTON
R
53. 0
09/08/94
CHC
362
430
Female
HOLSTON
R
53.0
11/29/94
CHC
554
1728
Male
HOLSTON
R
53.0
11/29/94
CHC
503
1135
Male
HOLSTON
R
53. 0
11/29/94
CHC
492
1032
Male
HOLSTON
R
53.0
11/29/94
CHC
0
0
Female
HOLSTON
R
76.0
09/08/94
CHC
453
812
Female
HOLSTON
R
76. 0
09/08/94
CHC
506
1300
Male
HOLSTON
R
76.0
09/08/94
CHC
445
712
Female
HOLSTON
R
76.0
09/08/94
CHC
364
484
Female
HOLSTON
R
76.0
09/08/94
CHC
370
560
Female
Male
Female
Female
Male
Male
Female
Female
Female
Female
OCOEE R 12.0
11/08/94
CHC
415
634
Male
OCOEE R 12.0
11/08/94
CHC
550
1680
Male
OCOEE R 12.0
11/08/94
CHC
465
965
Female
OCOEE R 12.0
11/08/94
CHC
505
1139
Female
OCOEE R 12.0
11/08/94
CHC
464
837
Female
OCOEE R 16.0
11/16/94
CHC
545
1608
Female
OCOEE R 16.0
11/16/94
CHC
484
1099
Female
OCOEE R 16.0
11/16/94
CHC
470
978
Female
OCOEE R 16.0
11/16/94
CHC
463
807
Male
OCOEE R 16.0
11/16/94
CHC
543
1588
Male
WHEELER
TENNESSEE R
277
10/27/94
CHC
477
953
Female
TENNESSEE R
277
10/27/94
CHC
442
636
Female
TENNESSEE R
277
11/02/94
CHC
440
772
Male
TENNESSEE R
277
11/02/94
CHC
344
295
Female
TENNESSEE R
277
11/08/94
CHC
511
1420
Female
TENNESSEE R
296
11/07/94
CHC
510
1140
Female
m^vtrTTTSSEE R
296
11/07/94
CHC
441
740
Female
JSSEE R
296
11/07/94
CHC
475
1000
Female
i it i^jS S EE R
296
11/07/94
CHC
505
1340
Female
TENNESSEE R
296
11/07/94
CHC
600
2380
Male
Page 1
-------
rable A-5
Specific physical information on composite fish collected for tissue
otroam and reservoir locations as part of^screening studies.
:o ion
Site
Date
Species
Length (mm)
Taur s«t"«A
Weight(g)
Sex
3SEE
R
347
11/03/94
CHC
495
1160
Female
TENNESSEE
R
347
11/03/94
CHC
485
1120
Female
TENNESSEE
R
347
11/03/94
CHC
474
980
Female
TENNESSEE
R
347
11/03/94
CHC
545
1240
Male
TENNESSEE
R
347
11/03/94
CHC
581
2120
Female
Page 2
-------
Table A-f
Specific physical
C " :ion Site Date
IlCK
TENNESSEE
R
469
11/18/94
TENNESSEE
R
469
11/18/94
TENNESSEE
R
469
11/21/94
TENNESSEE
R
469
11/21/94
TENNESSEE
R
469
11/21/94
TENNESSEE
R
469
11/21/94
TENNESSEE
R
469
11/21/94
TENNESSEE
R
469
11/21/94
TENNESSEE
R
469
11/21/94
TENNESSEE
R
469
11/21/94
information on individual fish collected for
reservoir locations as part of ggpooning studies.
Species Length(mm) Weight(g) Sex LABID
STB
872
8809
Female
STB
774
5179
Female
STB
1010
12500
Female
STB
874
7627
Female
STB
776
5590
Male
STB
804
7711
Female
STB
791
6330
Male
STB
937
9895
Female
STB
830
7917
Female
STB
852
8309
Female
Page 1
-------
Table A-5
Specific physical information on composite fish
atroam and reservoir locations as part of
collected for tissue
|»\ inJniTf'M
studies.
Cc'
Tl!
:ion Site
Date
Species Length(mm) Weight(g) Sex
LABID
LITTLE
TENNESSEE
R
10/20/94
CHC
614
2353
Male
LITTLE
TENNESSEE
R
10/20/94
CHC
474
951
Female
LITTLE
TENNESSEE
R
10/20/94
CHC
570
1970
Female
LITTLE
TENNESSEE
R
10/20/94
CHC
425
667
Male
LITTLE
TENNESSEE
R
10/20/94
CHC
461
999
Female
LITTLE
TENNESSEE
R
10/21/94
CHC
684
3739
Female
LITTLE
TENNESSEE
R
10/21/94
CHC
565
1621
Female
LITTLE
TENNESSEE
R
10/21/94
CHC
595
1856
Female
LITTLE
TENNESSEE
R
10/21/94
CHC
572
1654
Female
LITTLE
TENNESSEE
R
10/21/94
CHC
524
1259
Female
NICKAJACK
TENNESSEE
R
425
10/10/94
CHC
591
2841
Male
TENNESSEE
R
425
10/10/94
CHC
538
1865
Female
TENNESSEE
R
425
10/10/94
CHC
535
1484
Male
TENNESSEE
R
425
10/10/94
CHC
482
1023
Female
TENNESSEE
R
425
10/10/94
CHC
511
1156
Female
TENNESSEE
R
457
11/09/94
CHC
486
975
Female
TENNESSEE
R
457
11/09/94
CHC
516
1331
Female
TENNESSEE
R
457
11/09/94
CHC
599
2140
Male
,SSEE
R
457
11/09/94
CHC
556
1540
Male
;ssee
R
457
11/09/94
CHC
627
2790
Female
TENNESSEE
R
457
11/09/94
CHC
0
154
Female
CHICKAMAUGA
TENNESSEE
R
529
10/20/94
CHC
527
1335
Male
TENNESSEE
R
529
10/20/94
CHC
546
1628
Male
TENNESSEE
R
529
10/20/94
CHC
542
1445
Male
TENNESSEE
R
529
10/20/94
CHC
523
1198
Male
TENNESSEE
R
529
10/20/94
CHC
523
1546
Female
WATTS BAR
TENNESSEE
R
530
10/28/94
CHC
520
1259
Female
TENNESSEE
R
530
10/28/94
CHC
480
1013
Male
TENNESSEE
R
530
10/28/94
CHC
400
511
Male
TENNESSEE
R
530
11/22/94
CHC
637
2338
Male
TENNESSEE
R
530
11/22/94
CHC
492
943
Female
TENNESSEE
R
530
10/28/94
SBU
580
3109
Male
TENNESSEE
R
530
10/28/94
SBU
570
3160
Male
TENNESSEE
R
530
11/22/94
SBU
510
1892
Female
TENNESSEE
R
530
11/22/94
SBU
645
4655
Female
TENNESSEE
R
530
11/22/94
SBU
532
2695
Male
TENNESSEE
R
560
11/09/94
CHC
424
523
Male
SSEE
R
560
11/09/94
CHC
483
969
Male
i i-unN i^S SEE
R
560
11/09/94
CHC
522
1547
Male
TENNESSEE
R
560
11/09/94
CHC
607
2394
Male
Page 1
-------
Table A-5"
Specific physical information on composite fish collected for tissue
I OI/VT »»\0« iT»»- " W.S
Gtream and reservoir locations as part of aGreening studies.
c"1 ^-'¦ion
Site
Date
Species
Length(mm)
Weight(g)
Sex
ISEE
R
560
11/09/94
CHC
484
1076
Female
TENNESSEE
R
560
11/23/94
SBU
478
1685
Male
TENNESSEE
R
560
11/23/94
SBU
463
1427
Male
TENNESSEE
R
560
11/23/94
SBU
520
1982
Female
TENNESSEE
R
560
11/23/94
SBU
451
1245
Male
TENNESSEE
R
560
11/30/94
SBU
556
2880
Male
TENNESSEE
R
600
10/26/94
CHC
396
507
Female
TENNESSEE
R
600
10/26/94
CHC
395
496
Female
TENNESSEE
R
600
10/26/94
CHC
406
522
Female
TENNESSEE
R
600
11/23/94
CHC
659
2348
Female
TENNESSEE
R
600
11/30/94
CHC
490
919
Male
TENNESSEE
R
600
10/26/94
SBU
607
3643
Female
TENNESSEE
R
600
10/26/94
SBU
507
1946
Male
TENNESSEE
R
600
10/26/94
SBU
572
3066
Male
TENNESSEE
R
600
10/26/94
SBU
485
1737
Male
TENNESSEE
R
600
11/23/94
SBU
586
3230
Female
Page 2
-------
Tajble A-^
Specific physical
tissue otroam and
c
F
ion Site
UDOUN
Date
information on individual fish collected for
/»nc~+c.r»y "TOfitA.c
reservoir locations as part of aogaaning studies
Length(mm) Weight(g)
Species
Sex
LABID
TENNESSEE
R
624
10/04/94
CHC
480
1166
Male
TENNESSEE
R
624
10/04/94
CHC
390
500
Male
TENNESSEE
R
624
10/04/94
CHC
485
1026
Male
TENNESSEE
R
624
10/04/94
CHC
385
442
Male
TENNESSEE
R
624
10/04/94
CHC
662
2676
Female
TENNESSEE
R
624
10/05/94
CHC
417
538
Male
TENNESSEE
R
624
10/05/94
CHC
455
822
Male
TENNESSEE
R
624
10/05/94
CHC
416
515
Female
TENNESSEE
R
624
10/05/94
CHC
365
425
Male
Page 1
-------
Appendix B
Recommendations for fish tissue studies in 1995
-------
Study Type/Location
Appendix B. Recommendations for fish tissue studies in 1995*
River Mile Species # Needed Ind/Comp Analvtes
Reservoir Screening
Kentucky Res.
TRM 30
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
TRM 85
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
TRM 206
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
BSRM 7
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
Normandy Res
DRM250
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
Beech Res
IjJeRM 36
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
LMB
5
Composite
Mercury only
Tims Ford Res
ERM 135
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
ERM 150
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
Chickamauga Res
TRM 472
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
TRM 490
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
TRM 529
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
HiRM 8
CHC
5
Composite
Screening - Metals and Organics
LMB
5
Composite
Mercury only
-------
Study Type/Location River Mile
Reservoir Screening, cont.'
Fort Loudoun Res TRM 603
TRM624
TRM 652
Fort Pat. Res HRM 9
Stream Screening
Clarks River C1RM 10
Appendix B, Continued
Species fl Needed Ind/Comp
CHC 5 Composite
LMB 5 Composite
CHC 10 Ind+Comp
LMB 5 Composite
CHC 5 Composite
LMB 5 Composite
CHC 5 Composite
LMB 5 Composite
CHC 5 Composite
LMB 5 Composite
5 Composite
5 Composite
5 Composite
5 Composite
5 Composite
5 Composite
5 Composite
5 Composite
5 Composite
5 Composite
5 Composite
5 Composite
Analvtes
Screening - Metals and Organics
Mercury only
Comp = Screening - Metals/Organics
Ind = PCBs, DDTr, Chlordane
Mercury only
Screening - Metals and Organics
Mercury only
Screening - Metals and Organics
Mercury only
Screening - Metals and Organics
Mercury only
Screening - Metals and Organics
Mercury only
Screening - Metals and Organics
Mercury only
Screening - Metals and Organics
Mercury only
Screening - Metals and Organics
Mercury only
Screening - Metals and Organics
Mercury only
Screening Metals and Organics
Mercury only
Buffalo River BuRM 18 CHC
SMB
Bear CreekRiver BCM 27 CHC
LMB
Sequatchie River SeRM 10 CHC
LMB
Ocoee River ORM 4 CHC
LMB
Tuckasegee River TuRM 10 CHC
SMB
Holston River HRM 110 CHC
LMB
-------
Appencix B, Continued
Study Type/Location
River Mile Species
# Needed Ind/Comp
Arialvtes
Stream Screening, cont.'
N. Fork Holston R NFHRM 4
Pigeon River
Targeted Screenine
Wheeler Res
Cherokee
Nickajack Res
Parksville Res
PiRM
TRM 277
TRM295
TRM 347
E1RM 6
HRM 53
HRM76
TRM 469
ORM 12
ORM 16
CHC
SMB
CHC
SPB
CHC
CHC
CHC
CHC
CHC
STB
CHC
STB
STB
CHC
CHC
5
5
5
5
5
5
5
5
5
5
5
5
Composite Screening - Metals and Organics
Composite Screening - Mercury only
Composite Screening - Metals and Organics
Composite Mercury only
Composite PCBs, DDTr, Chlordane
Composite PCBs, DDTr, Chlordane
Composite PCBs, DDTr, Chlordane
Composite PCBs, DDTr, Chlordane
Composite PCBs, DDTr, Chlordane
Composite PCBs, DDTr, Chlordane
Composite PCBs, DDTr, Chlordane
Composite PCBs, DDTr, Chlordane
Composite PCBs, DDTr, Chlordane
Composite PCBs, DDTr, Chlordane
Composite PCBs, DDTr, Chlordane
Intensive Study
Note: The only Intensive study under consideration at the time this document was prepared was on
Wheeler Reservoir—four locations in the vicinity of Indian Creek (3 replicates of CHC, LMB, and SMB).
The primary study objective would be to determine if DDTr concentrations were sufficiently low for the
Alabama Department of Public Health to alter or remove the fish consumption advisory in that section of
the Tennessee River. Final decision on this study effort was to be made at a later date.
-------
TENNESSEE VALLEY AUTHORITY
Resource Group
Water Management
Clean Water Initiative
I
TENNESSEE VALLEY RESERVOIR AND STREAM QUALITY - 1993
FISH TISSUE STUDIES
IN THE TENNESSEE VALLEY IN 1993
Prepared by
Donald L. Williams
Fish and Wildlife Associates
Donald L. Dycus
Tennessee Valley Authority
Clean Water Initiative
Chattanooga, Tennessee
July 1994
-------
CONTENTS
Page
Tables iv
Figures vii
Executive Summary viii
I.0 Introduction 1
2.0 Kentucky Reservoir Watershed 4
3.0 Duck River Watershed 6
4.0 Pickwick Reservoir - Wilson Reservoir Watershed 8
5.0 Wheeler Reservoir - Elk River Watershed 11
6.0 Guntersville Reservoir - Sequatchie River Watershed 34
7.0 Chickamauga Reservoir - Nickajack Reservoir Watershed 36
8.0 Hiwassee River Watershed 49
9.0 Watts Bar Reservoir - Fort Loudoun Reservoir - Melton Hill Reservoir Watershed 53
10.0 Clinch River-Powell River Watershed 82
II.0 Little Tennessee River Watershed 85
12.0 French Broad River Watershed 89
13.0 Holston River Watershed 92
- References 97
Appendix A - Fish Tissue Screening Data for Reservoir and Stream Monitoring Sites, 1993 101
Appendix B - Chronological Listing of TVA Reports Relating to Toxics in Fish 121
Appendix C - Rationale and Procedures for Collection, Processing, and Analysis of Fish
Tissue Samples 127
Appendix D - State of Tennessee - Latest Fish Advisory 143
Appendix E - Alabama Department of Public Health Fish Consumption Advisories for the
Indian Creek Embayment (September 30,1991) on Wheeler Reservoir and Selected Portion
of Wheeler Reservoir (November 16,1992) 147
Appendix F - Mercury Concentrations in Largemouth Bass from Tributary Reservoirs 153
iii
-------
TABLES
Page
1-1 Contaminant concentrations used as the guideline for planning the level of continued
fish tissue studies in the Tennessee Valley waters 3
5.3-1 Physical information for individual fish collected from Wheeler Reservoir, 1993 19
5.3-2 Concentrations (jig/g) of organics in composite samples from Wheeler Reservoir, 1993 23
5.3-3 Summary of weight, length, and percent lipid content in catfish, largemouth bass and
smallmouth buffalo from Wheeler Reservoir, 1991-1993 24
5.3-4 Two-way analysis of variance (location and year main effects) and Ryan-Einot-Gabriel-
Welsch Multiple Range Test on lipid content and total weight in catfish, largemouth
bass, and smallmouth buffalo from Wheeler Reservoir, 1991-1993 25
5.3-5 One-way analysis of variance and Ryan-Einot-Gabriel-Welsch Multiple Range Test
on total weight in channel catfish collected from Wheeler Reservoir, 1991 -1993 26
5.3-6 Summary of total PCB concentrations (ng/g) in catfish, largemouth bass and smallmouth
buffalo composites from Wheeler Reservoir, 1991-1993 27
5.3-7 Summary of total DDT concentrations (ng/g) in catfish, largemouth bass and smallmouth
buffalo composites from Wheeler Reservoir, 1991-1993 28
5.3-8 Two-way analysis of variance (location and year main effects) and Ryan-Einot-Gabriel-
Welsch Multiple Range Test on PCB and DDT concentrations in cattish, largemouth
bass, and smallmouth buffalo from Wheeler Reservoir, 1991-1993 29
5.3-9 One-way analysis of variance (location effects) and Ryan-Einot- Gabriel-Welsch
Multiple Range Test on PCB and DDT concentrations in channel catfish, largemouth
bass and smallmouth buffalo from Wheeler Reservoir, 1993 30
5.3-10 One-way analysis of variance (year effects) and Ryan-Einot-Gabriel- Welsch Multiple
Range Test on PCB concentrations among years for each location in channel catfish,
largemouth bass, and smallmouth buffalo from Wheeler Reservoir, 1993 31
5.3-11 One-way analysis of variance (year effects) and Ryan-Einot-Gabriel- Welsch Multiple
Range Test on DDT concentrations in smallmouth buffalo from Wheeler Reservoir, 1993 32
5.3-12 DDT concentrations (ng/g wet weight) in composites of channel catfish, largemouth
bass, and smallmouth buffalo from Wheeler Reservoir, 1991-1993 33
7.2-1 Physical data and analyte concentrations (ng/g) in carp, channel catfish, and striped
bass from Nickajack Reservoir, 1993 40
7.2-2 Summary of lengths, total weights, and percent lipids of catfish, carp, and
striped bass from Nickajack Reservoir, collected from 1988 to 1993 42
7.2-3 Two-way analysis of variance (location and year main effects) and Ryan-Einot-
Gabriel-Welsch Multiple Range Test on lipid content and total weight in catfish and
carp from Nickajack Reservoir, 1988-1993 43
-------
TABLES
Page
7.2-4 One-way analysis of variance and Ryan-Einot-Gabriel-Welsch Multiple Range Test
on total weight in channel catfish from Nickajack Reservoir, 1988-1993 44
7.2-5 Summary of total PCB concentrations (ng/g) in individual catfish, carp, smallmouth
buffalo, and striped bass fillets from Nickajack Reservoir, collected from 1988 to 1992 45
7.2-6 Two-way analysis of variance* (location and year main effects) and Ryan-Einot-
Gabriel-Welsch Multiple Range test on PCB concentrations in catfish and carp from
Nickajack Reservoir, 1988-1993 46
7.2-7 One-way analysis of variance and Ryan-Einot-Gabnel-Welsch Multiple Range test on
PCB concentrations in carp from Nickajack Reservoir, 1991-1993 47
7.2-8 One-way analysis of variance (year effects) and Ryan-Einot-Gabriel-Welsch Multiple
Range test on lipid content, total weight, and PCB concentrations in striped bass from
TRM 469, Nickajack Reservoir, 1992-1993 48
9.3.1-1 Physical information for channel catfish, carp, white bass, and smallmouth buffalo
collected from Watts Bar Reservoir, 1993 57
9.3.1-2 Concentrations of analytes in channel catfish, carp, white bass, and smallmouth buffalo
collected from Watts Bar Reservoir, 1993 59
9.3.1-3 Summary of lengths, total weights, and percent lipids of catfish from the Tennessee
River portion of Watts Bar Reservoir, 1993 and previous years 60
9.3.1-4 Summary of lengths, total weights, and percent lipids of catfish from the Clinch River
portion of Watts Bar Reservoir, 1993 and previous years 61
9.3.1-5 Two-way analysis of variance (location and year main effects) and Ryan-Einot-
Gabriel-Welsch Multiple Range Test on lipid content and total weight in channel
catfish from Watts Bar Reservoir, 1988-1993 62
9.3.1-6 Summary of total PCB concentrations (jig/g) in catfish fillets from Watts Bar
Reservoir, 1987 to 1993 63
9.3.1-7 Results of Two-Way Analysis of Variance used to compare location and year differences
in PCB concentrations in channel catfish from Watts Bar Reservoir, 1993 64
9.3.1-8 One-Way Analysis of Variance and Ryan-Einot- Gabriel-Welsch Multiple Range Test
comparing year differences for individual sites in PCB concentrations in channel catfish
from Watts Bar Reservoir, 1993 64
9.3.1-9 Summary of lengths, total weights, percent lipids, and PCB concentration in white
bass from Watts Bar Reservoir, 1993 and previous years 65
9.3.1-10Summary of lengths, total weights, percent lipids, and PCB concentration in carp
from Watts Bar Reservoir, 1993 and previous years 66
v
-------
TABLES
Page
9.3.1-11 Summary of lengths, total weights, percent lipids, and PCB concentration in
smallmouth buffalo from Watts Bar Reservoir, 1993 and previous years 67
9.3.2-1 Physical data and analyte concentrations (|ig/g) in channel catfish collected from
TRM 624, Fort Loudoun Reservoir, on November 12, 1993 70
9.3.2-2 Summary of lengths, total weights, and % lipids of catfish, carp, and white bass
from Fort Loudoun Reservoir, collected from 1985 to 1993 73
9.3.2-3 Results of one-way ANOVA and REGW Multiple Range Test examining differences
among years in lipid content and total weight in catfish from TRM 624-629, Fort
Loudoun Reservoir 74
9.3.2-4 Summary of PCB concentrations in catfish, carp, and white bass from Fort Loudoun
Reservoir, collected from 1985 to 1993 75
9.3.2-5 Results of statistical tests used to compare yearly differences in PCB concentrations
in catfish from TRMs 624-629, Fort Loudoun Reservoir, 1985-1993 76
9.4.1-1 Physical information, lipid content, PCB, and chlordane concentrations of channel
catfish and carp composites collected for the three embayment study on Melton
Hill Reservoir, 1993 80
13.3-1 Results of the special study conducted on lead and mercury concentrations in channel
catfish and largemouth bass from Cove Spring Branch Embayment, South Holston
Reservoir, 1993 96
A-l Specific physical.information on individual fish collected for tissue analysis from stream
and reservoir locations as part of screening studies, 1993 102
A.2 Concentrations (|ig/g) of organics in composited fish samples from stream and
reservoir monitoring locations, 1993 114
A-3 Concentrations (ng/g) of metals in composited fish flesh samples from stream and
reservoir monitoring locations, 1993 118
F-l Physical information and concentrations (fig/g) of total mercury in individual and
composited largemouth bass in the Tennessee Valley in 1993 156
vi
-------
FIGURES
Page
9.3.1-1 Mean PCB Concentrations (|ig/g) in Catfish from Individual Sites, TRM 530-532,
TRM 557-562, TRM 570-573, and TRM 598-600, on Watts Bar Reservoir, 1987-1993 68
9.3.2-1 Mean PCB concentrations (ng/g) in catfish from TRM 624 on Fort Loudoun
Reservoir, 1985-1993 77
9.4-1 Locations of the Three Embayments Sampled in 1993 from Melton Hill Reservoir 81
F-l Regression of mercury concentration vs total weight of largemouth bass from tributary
reservoirs in the Tennessee Valley in 1993 160
vii
-------
EXECUTIVE SUMMARY
TV A has been involved in fish tissue studies for a number of years. Because of the
significant interest expressed by Valley states and the fishing public, TVA's involvement in
these studies has continued from year to year. TVA coordinates these efforts with state and
federal agencies to avoid duplication.
TVA analyzes tissues of Tennessee Valley fish as part of both intensive and screening
evaluations. Screening studies are conducted to identify sites having potential contamination
problems. Intensive studies are conducted to define the extent of problems identified by
screening studies.
Fish collected for screening studies are usually analyzed for metals, PCBs, and
pesticides on EPA's Priority Pollutant List. Fish for intensive studies are analyzed only for
the contaminant of concern, which has been identified by screening studies, or is known as an
historic problem. Lipid content is determined on all samples.
Principal results of fish tissue studies in 1993 were:
(1). Screening studies did not indicate a need for new intensive studies, although other
studies are warranted (see item 2 below).
(2). Largemouth bass were collected from tributary reservoirs as part of reservoir
screening studies and were analyzed as composites for mercury. Many large fish
(1200+ grams) were also analyzed as individuals in an attempt to describe worst-case
conditions. Relatively high concentrations of mercury in many of these fish from
tributary reservoirs, especially large fish, indicate a need for further examination.
viii
-------
PCB concentrations in fish from Nickajack, Watts Bar, and Fort Loudoun Reservoirs
continued to be high. Continued monitoring of these reservoirs is recommended.
DDTr concentrations in fish collected near the Indian Creek embayment on Wheeler
Reservoir were relatively high in some samples, especially smallmouth buffalo.
Continued examination in this area is recommended to help document chages through
time.
Fish collected near a former battery dumpsite in Cave Spring Branch Embayment of
South Holston Reservoir contained levels of mercury and lead consistent with levels
in fish from other reservoirs indicating no impact from the battery dump.
Fish were collected from three embayments near CRM 51 on Melton Mil Reservoir to
determine why previous studies have typically found one or two fish in that area with
unusually high PCB concentrations. Although a more in-depth study would be
necessary to rule out these embayments as potential contributors of high PCB
concentrations in fish collected in previous years, results of this special study do not
support the need for a more in-depth investigation.
IX
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FISH TISSUE STUDIES
IN THE TENNESSEE VALLEY IN 1993
1.0 INTRODUCTION
TVA analyzes tissues of Tennessee Valley fish as part of both screening and intensive
evaluations. Screening studies are based on analysis of composited fillets and are intended to
identify possible problem areas where intensive investigations may be needed. Table 1-1 includes
the contaminant concentrations used as the guidelines for planning follow-up fish tissue studies.
Sites with fish containing concentrations less than those listed as Tier 1 are sampled on a
three-year rotation. Sites with fish containing contaminant concentrations higher than the values
listed under Tier 2 are sampled at the screening level the following year. Sites with fish
containing levels above Tier 3 are in nedd of intensive investigation.
Intensive studies usually include analysis of individual fillets from important fish species
from several areas in the reservoir. The primary objectives of intensive studies are to define the
species affected, geographical boundaries of contamination, and to document trends in
contaminant concentrations. This information is used by state public health officials to determine
if fish consumption advisories are necessary to protect human health.
Included in the screening study are reservoir and stream monitoring locations. There are
about 80 reservoir sites which are generally monitored on a three-year rotational basis. There are
11 stream monitoring locations which have been sampled on an annual basis through 1993. Six
additional stations will be included in 1994, and a two year on, one year off rotation will be
implemented.
1
-------
The results from both intensive studies and screening studies conducted in 1993 are
provided in this report. Originally a separate report was written for the intensive and screening
studies. However, the screening and intensive studies for 1989 were combined into one report
with separate chapters for each type of study. The same format was followed for the 1990 and
1991 and 1992 reports. In response to changing customer base and in keeping with TVA's focus
on watershed management, this report contains separate chapters on each watershed. Each
chapter begins with a drainage map of the watershed with designated sampling locations, followed
by an introduction, information on screening studies, information on any intensive studies
conducted within the watershed, and finally information on any special studies conducted within
the watershed. Appendix A contains physical information and results of chemical analyses for the
screening studies conducted in 1993. Appendix B is a chronological listing of TVA reports
relating to contaminants in fish. Appendix C identifies rationales and procedures used in the
collection, processing, and laboratory and data analysis of fish tissue samples. Appendix D is the
latest fish advisory information for water bodies in Tennessee. Appendix E includes 1991 and
1992 fish consumption advisories on Wheeler Reservoir in Alabama. Appendix F contains
information on special mercury analyses performed on selected largemouth bass (i.e. those
weighing over three pounds) collected as part of the fish tissue screening studies in 1993.
2
-------
Table 1-1 Contaminant concentrations8 used as guidelines for planning the level of continued
fish tissue studies in Tennessee Valley waters.
Parameter
Laboratory
Detection Limit
(ng/g)
Tier 1
Return to Rotation
System
(Hg/g)
Tier 2
Resample at
Screening Level
Following Year
(Hg/g)
Tier 3
Recommend
Intensive Study
(ng/g)
Arsenic 0.02
Cadmium 0.05
Lead
0.02
Mercury
0.1
Selenium
0.02
Aldrin
0.01
Benzene Hexachloride
0.01
Chlordane
0.01
DDT
0.01
Dieldrin
0.01
Endosulfan
0.01
Endrin
0.01
Heptachlor
0.01
Toxaphene
0.5
PCBs
0.1
<0.5 >0.5 £0.7
<0.5 £0.5 £1.0
<1.5 £1.5 £2.0
<0.5 £0.5 £0.7
<1.0 £1.0 >3.0
<0.1 >0.1 >0.2
<0.1 £0.1 £0.2
<0.1 £0.1 £0.2
<2.0 £2.0 £4.0
<0.1 £0.1 £0.2
<3.0 £3.0 £5.0
<0.1 >0.1 £0.2
<0.1 £0.1 £0.2
<2.0 >2.0 £3.0
<1.0 >1.0 £1.5
a. These levels will be used as a general guide. Specific recommendations will be made on a case-by-case basis.
b. Selection of a level for this metal, which would result in a recommendation to conduct intensive studies, cannot be made at this time.
3
-------
Ohio River
KY
Chapter 2
Kentucky Reservoir
Watershed
i —
TN
^Stream Monitoring Sites sampled in 1993
^Stream Monitoring Sites not sampled in 1993
^Reservoir Monitoring Sites sampled in 1993
QReservoir Monitoring Sites not sampled in 1993
Duck RivefWatershed
TN
MS
Pickwick Reservoir- A y
^Vilson Reservoir Watershed /\ I
-------
Chapter 2.0 Kentucky Reservoir Watershed
No fish tissue samples were taken from the Kentucky Reservoir Watershed in 1993
because the sites were sampled each year between 1988 and 1992 and contaminant concentrations
were either low or slightly elevated with no consistent temporal or spatial trends. Historical data
from monitoring sites within the Kentucky Reservoir Watershed are available in publications listed
in Appendix B.
5
-------
Kentucky Reservoir
Watershed
Pickwick Reservoir-Wilson Reservoir Watershed
Chapter 3
Duck River Watershed
A Stream Monitoring Sites sampled in 1993
A Stream Monitoring Sites not sampled in 1993
• Reservoir Monitoring Sites sampled in 1993
O Reservoir Monitoring Sites not sampled in 1993
-------
Chapter 3.0 Duck River Watershed
3.1 Introduction
In 1993, the only location in the Duck River Watershed where fish tissue samples were
collected was a stream monitoring site at DRM 22.5. No problems were found when the
reservoir monitoring sites on Normandy Reservoir were sampled in 1987, 1988, and 1992.
Therefore, these sites were not sampled in 1993. Publications describing historical data from
monitoring sites within the Duck River Watershed are in Appendix B.
3.2 Methods
Five channel catfish and four spotted bass were collected at DRM 22.5. These fish were
composited by species and analyzed for lipids, metals and organics. Field handling and processing
and laboratory processing were performed according to the methods outlined in Appendix C.
3.3 Results and Recommendations
Physical information and the results of metals and organics analyses are contained in
Appendix A along with data for other stream and reservoir monitoring sites. Metal and organic
analytes were below detection limits or found in low concentrations. This stream monitoring
station will be sampled in summer 1994 along with a new stream monitoring site on the Buffalo
River at approximately mile 17.7.
7
-------
Chapter 4
Pickwick Reservoir-
Wilson Reservoir Watershed
Duck River Watershed
Kentucky Reservoir
Watershed
Wheeler Reservoir Watershed
AL
Stream Monitoring Sites sampled in 1993
Stream Monitoring Sites not sampled in 1993
Reservoir Monitoring Sites sampled in 1993
Reservoir Monitoring Sites not sampled in 1993
-------
Chapter 4.0 Pickwick Reservoir-Wilson Reservoir Watershed
4.1 Introduction
Fish tissue samples were collected at only three reservoir monitoring sites in the Pickwick
Reservoir-Wilson Reservoir Watershed in 1993; Pickwick Reservoir inflow from Wilson Dam
(TRM 259), and the forebays of Bear Creek Reservoir (Bear Creek Mile 57) and Little Bear
Creek Reservoir (Little Bear Creek Mile 12). The Pickwick Reservoir inflow site was sampled
because of a high DDT level (2.5 pg/g) evident in the composite sample of channel catfish from
this location in 1992. The sites on Bear Creek and Little Bear Creek Reservoirs were sampled
because of high levels of mercury (0.45 and 0.56 pg/g, respectively) in channel catfish composites
from these sites in 1992. Publications containing historical data from monitoring sites within the
Pickwick Reservoir-Wilson Reservoir Watershed are in Appendix B.
4.2 Methods
A composite sample of five channel catfish was collected from Pickwick Reservoir inflow.
Composites of five channel catfish and five largemouth bass were collected from the forebays of
Bear Creek Reservoir and Little Bear Creek Reservoir. Catfish samples were analyzed as
composites for pesticides, PCBs, selected metals on the EPA Priority Pollutant List and lipids.
Largemouth bass samples were analyzed as composites only for mercury. In addition to
composite analysis, each largemouth bass that weighed more than 1200 grams was analyzed
individually for mercury; results for these individual analyses are included in Appendix F. Field
handling and processing and laboratory processing were performed according to the methods for
screening studies outlined in Appendix C.
9
-------
4.3 Results and Recommendations
Physical information and the results of metals and organics analyses are included in
Appendix A. None of the metal or organic analytes in channel catfish from Pickwick Reservoir
inflow (TRM 259) were sufficiently high to warrant resampling in 1994. Except mercury,
analytes were either not detected or found in low concentrations in samples from Little Bear
Creek and Bear Creek Reservoirs. Mercury concentrations in both channel catfish (0.66 ng/g)
and largemouth bass (0.71 ng/g) from Bear Creek Reservoir and largemouth bass (0.60 ng/g)
from Little Bear Creek Reservoir were sufficiently high to warrant further investigation in autumn
1994.
10
-------
Ch..r :er 5
Wheeler Reservoir - Elk River Watershed
TRMs 308.315.320. and 325
A special cooperative study between TVA
and Alabama officials on DDT and PCB
contamination near the Huntsville Spring
Branch tributary of the Tennessee River was
continued in 1993. DDT levels were
generally lower in 1993 than previous years
with fish from TRM 320 having higher
concentrations than the other sites. PCB
levels in catfish were higher at upstream
locations.
TRM 347
Elevated levels of PCBs (1.4 ng/g) and
chlordane (0.15 ng/g) in catfish warTant ;
continued screening of this statioa
-MM,MUM MM, f;
• Reservoir Monitoring Sites sampled in 1993
O Rejservoir Monitoring Sites not sampled in 1993
A Stream Monitoring Sites sampled in 1993
A Stream Monitoring Sites not sampled in 1993
¦ Wheeler DDT Study
AL
-------
Chapter 5.0 Wheeler Reservoir - Elk River Watershed
5.1 Introduction
The Tennessee Department of Environment and Conservation (TDEC) has issued a fish
consumption advisory against consuming catfish caught in Woods Reservoir, a non-TVA
reservoir, because of PCB contamination (Appendix D). The Alabama Department of Public
Health has also issued advisories against consuming certain fish caught in selected areas of
Wheeler Reservoir because of DDT contamination (Appendix E).
Fish for screening purposes were collected from four locations in Wheeler Reservoir - Elk
River Watershed for fish tissue screening studies in 1993. Three of these locations were reservoir
monitoring sites (TRM 277, TRM 296, and TRM 347). The fourth location was a stream
monitoring site at ERM 41.5. Fish for intensive study purposes were collected from four other
locations in Wheeler Reservoir, TRMs 308, 315, 320, and 325, as part of the continuing study of
DDT near the Indian Creek embayment. Historical data from monitoring sites within the Wheeler
Reservoir - Elk River Watershed are available in publications listed in Appendix B.
5.2 Screening Studies
5.2.1 Methods
Five channel catfish were collected from TRMs 277, 296, and 347 and ERM 41.5 in 1993.
Four largemouth bass were also collected from ERM 41.5. These fish were analyzed as
composites for lipids, pesticides, PCBs, and selected metals on the EPA Priority Pollutant List.
Field handling and processing and laboratory processing were performed according to the
methods outlined in Appendix C.
12
-------
5.2.2 Results and Recommendations
Physical information and the results of metals and organics analyses for channel catfish and
largemouth bass composites from Wheeler Reservoir and the Elk River are contained in Appendix
A, along with data for other stream and reservoir monitoring sites. Contaminant levels in fish
from ERM 41.5 and TRM 277 were not high enough to warrant concern. Chlordane levels in
channel catfish from TRM 296 (0.16 (ig/g) and chlordane (0.15 |ig/g) and PCB (1.4 ng/g) levels
in channel catfish from TRM 347 warrant further efforts.
Screening efforts at TRMs 296 and 347 as well as TRM 277 will be continued in autumn
1994 to further investigate the elevated chlordane and PCB concentrations found in 1993. Elk
River Mile 41.5 will be sampled in summer 1994 because of relatively high mercury
concentrations found in previous years.
5.3 Wheeler DDT Study
5.3.1 Introduction
The Alabama Department of Public Health (ADPH) issued a fish consumption advisory
for several fish species from the Indian Creek drainage area of Wheeler Reservoir in September
1991 due to DDT contamination. This was a historic problem area but an advisory had not been
issued previously. To evaluate the possible need to extend the advisory into the Tennessee River,
a special study was designed by TVA and Alabama officials and conducted in fall 1991. Based on
the 1991 results, the ADPH extended the advisory on selected species into the Tennessee River.
Details of the species and locations for the latest advisory are in appendix E.
As a result of the high concentrations found in 1991, the study was scheduled to be
repeated in autumn 1992. Because of technical difficulties, fish were not collected until January
1993. Concentrations ofDDTr (total DDT) were substantially lower in the fish collected in
13
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January 1993 (collections made in January 1993 will be referred to as 1992 collections throughout
the remainder of this section). These lower concentrations prompted TVA and Alabama officials
to continue the study in autumn 1993.
5.3.2 Methods
The design of the special study was established by TVA and the Alabama Departments of
Public Health, Environment Management, and Conservation. The design specified three, 5-fish
composites of each of three species (channel catfish, largemouth bass and smallmouth buffalo) to
be collected from four locations (TRMs 308, 315, 320 near the mouth of the Indian Creek
embayment, and 325). The sampling effort was successful as planned in autumn 1993.
Field handling and processing were similar to the methods described in appendix C.
Several fish collected for this study were shared with a group of researchers from the Registry of
Tumors in Lower Animals, National Museum of Natural History, Smithsonian Institution,
Washington, D.C. External, internal, and sex observations for these fish were not recorded.
The laboratory analyses for lipids, PCBs, and DDTr were conducted similar to the
screening study methods described in appendix C. Ortho-para isomers of DDT, DDD, and DDE
were examined in addition to the routine examination of para-para isomers.
Statistical analyses for these results varied from that described in Appendix C in that
covariance analyses were not performed because laboratory analyses were conducted on
composites preventing examination of relationships between contaminant concentration and fish
weight or lipid content. One-way and two-way ANOVAs were performed.
Included in the design of this special study was the sharing between TVA and Alabama
Department of Environmental Management (ADEM) of aliquots of homogenized fish tissue from
one composite sample of each species (channel catfish, smallmouth buffalo, and largemouth bass)
14
-------
from each sampling location (TRMs 308, 315, 320 and 325). These aliquots, 12 for each year,
were analyzed by TVA and ADEM laboratories for PCBs, chlordane and para-para DDT, DDD
and DDE concentrations and lipid content. Results from these split samples for 1991 and 1992
were provided in Williams and Dycus, 1993. Results from the 1993 split samples were not
available at the time this report was prepared.
5.3.3 Results and Recommendations
All results are presented in tables 5.3-1 through 5.3-11. Neither weights nor lipid content
of largemouth bass or smallmouth buffalo were significantly different among locations or years.
This was not the case for channel catfish, both lipid content and weight were significantly
different. Lipid concentrations in composite samples of channel catfish did not vary significantly
between locations but did vary among years with samples from 1991 having significantly higher
lipid content than ones from 1992 and 1993. Catfish weight distribution varied among years,
resulting in a significant interaction between year and location. Larger catfish were collected from
all locations in 1991 compared to the other two years. When locations were examined by years,
test results varied substantially (Table 5.3-5). In 1993 catfish from TRM 325 weighed
significantly less than individuals from the other three sites.
DDT concentrations were highest in all species in 1991. At least one composite of one
species exceeded 5 ug/g at each site. Highest concentrations were in smallmouth buffalo
(maximum 43 ug/g) from near the mouth of Indian Creek. Largemouth bass tended to have lower
concentrations than the other two species.
Samples for 1992 had substantially lower concentrations than observed in 1991. Of the 36
samples for 1992, only two exceed 5 ug/g, while 15 collected in 1991 exceeded that
concentration. Highest concentrations in 1992 were in smallmouth buffalo (maximum of 9.2
15
-------
ug/g) and largemouth bass (maximum of 7.4 ug/g). Concentrations in channel catfish in 1992
(maximum of 3.1 ug/g) were much lower than in 1991 (maximum of 13 ug/g); none of the channel
catfish samples exceeded 5 ug/g in 1992 compared to seven of 12 exceeding that level in 1991.
In 1993, five of the 36 samples exceeded 5 ug/g; all from TRM 320 (near Indian Creek)
and TRM 325. Of these four were smallmouth buffalo (maximum of 21 ug/g) and one was
largemouth bass (maximum of 6.4 ug/g). As in 1992, all channel catfish samples had relatively
low concentrations (maximum of 2.8 ug/g). Smaller size and lower lipid content in catfish
collected in 1992 and 1993 may have contributed to this difference.
Two-way ANOVAs (location and year effects) were conducted on DDT concentrations in
channel catfish, largemouth bass, and smallmouth buffalo. DDT concentrations in channel catfish
samples collected in 1992 (January 1993) and 1993 were significantly lower than concentrations
in 1991. DDT concentrations in channel catfish were significantly lower at TRM 325 than at
TRMs 308 and 320. DDT concentrations in largemouth bass were not significantly different
among locations or years.
A significant interaction was found in smallmouth buffalo. The interaction was caused
primarily by differing trends in contaminant concentration among sites. One-way ANOVAs were
used as an indication of temporal differences at each location. At TRM 308 and TRM 315
smallmouth buffalo contained significantly less DDT in 1993 than in 1991. DDT concentrations
in buffalo were not significantly different in 1993 or 1991 at TRMs 320 and 325. When 1993
results were tested alone, smallmouth buffalo from the two upper sites (TRMs 320 and 325) had
significantly higher DDT levels than those from the two lower sites.
PCB concentrations in these samples were also tested for location effects using a
one-way ANOVA on 1993 results. PCB concentrations in channel catfish were significantly
higher at the uppermost site than at the lowermost site. PCB concentrations in largemouth bass
-------
and smallmouth buffalo were not significantly different among locations in 1993. Two-way
ANOVAs of PCB concentrations found significant interaction between location and year effects
for all three species included in the study.
Results for 1993 confirm that high concentrations of DDTr can be found in smallmouth
buffalo samples from Wheeler Reservoir near the Indian Creek embayment. Concentrations have
tended to be quite variable, especially among years. Substantial variability is expected based on
studies within the Indian Creek embayment conducted by Olin Corporation (1994). Individual
fish with high concentrations likely move out of the embayment into the Tennessee River.
Collection of one of these individuals and subsequent compositing with four other fish would
result in a high sample concentration relative to a composite without such an individual. Analysis
of individual fish would allow resolution of this question.
The temporal variation in DDTr concentrations in channel catfish during this three-year
period is unexpected. The first year of the study in 1991 identified high concentrations at several
sites. Greatly reduced concentrations in both 1992 and 1993 were unexpected. The existing
advisory covers a greater area for channel catfish than for the other species, primarily because of
the high concentrations at the sites from the downstream portion of the study area. Smaller fish
with lower lipid content may be an important consideration in these year-to-year differences.
Sampling of channel catfish in autumn 1994 with emphasis on larger individuals, comparable to
those in 1991, is needed to determine if the expanded advisory area is still warranted.
Results for largemouth bass during the three-year study have been somewhat perplexing,
especially for 1992 and 1993. The primary issue is the sporadic occurrence of high
concentrations; at times similar or higher than in channel catfish and smallmouth buffalo. Also,
some samples have had higher concentrations than in largemouth bass from the Indian Creek
embayment reported in the Olin Corporation studies (1994). These issues need further
17
-------
investigation. An analysis based on replicate individuals from the study area could help define
variation in the population.
Design of autumn-1994 studies will be determined based on these recommendations,
discussions with the Alabama Departments of Environmental Management, Public Health, and
Conservation, and availability of funding.
18
-------
Table 5.3-1 Physical information for individual fish collected from Wheeler Reservoir, 1993.
ollection Site
Date
Species'
Length (mm)
Weight (g)
Sex
LABID"
TRM 308
10
5
93
CHC
497
1225
FMALE
32604
TRM 308
10
5
93
CHC
438
755
FMALE
32604
TRM 308
10
7
93
CHC
469
935
FMALE
32604
TRM 308
10
7
93
CHC
431
795
FMALE
32604
TRM 308
10
7
93
CHC
447
990
MALE
32604
TRM308
10
7
93
CHC
525
1700
FMALE
32606
TRM 308
10
7
93
CHC
433
695
MALE
32606
TRM 308
10
7
93
CHC
470
1225
FMALE
32606
TRM308
10
7
93
CHC
421
595
FMALE
32606
TRM308
10
7
93
CHC
521
1605
FMALE
32606
TRM 308
10
7
93
CHC
424
690
FMALE
32609
TRM 308
10
19
93
CHC
525
1625
MALE
32609
TRM 308
10
19
93
CHC
521
1550
MALE
32609
TRM 308
10
19
93
CHC
435
745
MALE
32609
TRM 308
10
19
93
CHC
525
1590
MALE
32609
TRM 308
10
5
93
LMB
385
855
FMALE
32610
TRM 308
10
5
93
LMB
327
495
FMALE
32610
TRM 308
10
7
93
LMB
423
1075
FMALE
32610
TRM 308
10
7
93
LMB
350
725
FMALE
32610
TRM 308
10
20
93
LMB
305
350
FMALE
32610
TRM 308
10
20
93
LMB
315
425
FMALE
32611
TRM 308
10
20
93
LMB
315
375
FMALE
32611
TRM 308
10
20
93
LMB
322
445
FMALE
32611
TRM 308
10
20
93
LMB
329
440
FMALE
32611
TRM 308
10
20
93
LMB
366
705
FMALE
32611
TRM 308
10
20
93
LMB
375
650
FMALE
32612
TRM 308
10
20
93
LMB
305
330
FMALE
32612
TRM 308
10
20
93
LMB
321
395
FMALE
32612
TRM 308
10
20
93
LMB
516
2285
FMALE
32612
TRM 308
10
20
93
LMB
305
330
FMALE
32612
TRM 308
10
5
93
SBU
474
1565
MALE
32613
TRM 308
10
5
93
SBU
553
3030
MALE
32613
TRM 308
10
5
93
SBU
477
1665
MALE
32613
TRM 308
10
5
93
SBU
484
1850
MALE
32613
TRM 308
10
5
93
SBU
518
2065
MALE
32613
TRM 308
10
5
93
SBU
471
1805
MALE
32614
TRM 308
10
5
93
SBU
536
2440
MALE
32614
TRM 308
10
5
93
SBU
540
2565
MALE
32614
TRM 308
10
5
93
SBU
550
2795
FMALE
32614
TRM 308
10
5
93
SBU
502
2390
MALE
32614
TRM 308
10
5
93
SBU
470
1875
FMALE
32615
TRM 308
10
5
93
SBU
499
2100
MALE
32615
19
-------
LABID'
32615
32615
32615
33003
33003
33003
33003
33003
33005
33005
33005
33005
33005
33008
33008
33008
33008
33008
33009
33009
33009
33009
33009
33010
33010
33010
33010
33010
33011
33011
33011
33011
33011
33021
33021
33021
33021
33021
33022
33022
33022
33022
33022
33023
33023
33023
33023
33023
Date
Species* Length (mm) Weight (g) Sex
0
5
93
SBU
547
2525
MALE
0
5
93
SBU
431
1290
MALE
0
5
93
SBU
513
2340
MALE
2
93
CHC
531
1620
MALE
2
93
CHC
517
1320
FMALE
2
93
CHC
503
1440
FMALE
2
93
CHC
586
2370
FMALE
2
93
CHC
554
1540
MALE
2
93
CHC
486
1060
MALE
2
93
CHC
434
865
MALE
3
93
CHC
577
1895
FMALE
3
93
CHC
452
925
FMALE
3
93
CHC
455
1015
FMALE
3
93
CHC
479
1440
FMALE
3
93
CHC
528
1235
FMALE
3
93
CHC
477
960
MALE
3
93
CHC
482
1205
MALE
9
93
CHC
435
710
FMALE
1
93
LMB
381
700
FMALE
1
93
LMB
400
920
FMALE
1
93
LMB
347
375
FMALE
1
93
LMB
408
1045
FMALE
1
93
LMB
386
855
FMALE
1
93
LMB
355
560
FMALE
1
93
LMB
312
410
FMALE
1
93
LMB
306
345
FMALE
3
93
LMB
401
925
FMALE
3
93
LMB
382
695
MALE
3
93
LMB
345
625
FMALE
3
93
LMB
336
535
FMALE
3
93
LMB
323
485
FMALE
3
93
LMB
334
530
MALE
3
93
LMB
316
435
MALE
2
93
SBU
542
2510
MALE
2
93
SBU
431
1310
MALE
2
93
SBU
403
960
MALE
2
93
SBU
328
500
FMALE
2
93
SBU
366
465
FMALE
3
93
SBU
503
1825
MALE
3
93
SBU
557
3040
MALE
3
93
SBU
481
1815
MALE
3
93
SBU
439
1710
MALE
3
93
SBU
446
1495
MALE
3
93
SBU
496
1825
MALE
4
93
SBU
480
1630
MALE
4
93
SBU
424
1620
MALE
2
8
93
SBU
507
2145
FMALE
2
8
93
SBU
507
2145
FMALE
20
-------
LABID'
32618
32618
32618
32618
32618
32619
32619
32619
32619
32619
32620
32620
32620
32620
32620
32621
32621
32621
32621
32621
32623
32623
32623
32623
32623
32626
32626
32626
32626
32626
32627
32627
32627
32627
32627
32628
32628
32628
32628
32628
32629
32629
32629
32629
32629
33024
33024
33024
33024
33024
Date
Species' Length (mm) Weight (g) Sex
10
13
93
CHC
454
850
FMALE
10
13
93
CHC
490
1340
FMALE
10
13
93
CHC
523
1645
FMALE
10
13
93
CHC
542
1625
FMALE
10
13
93
CHC
457
975
FMALE
10
12
93
CHC
510
1400
c
10
12
93
CHC
470
930
c
10
12
93
CHC
440
750
c
10
22
93
CHC
538
1735
FMALE
10
22
93
CHC
450
665
MALE
10
22
93
CHC
494
1155
FMALE
10
26
93
CHC
476
1040
FMALE
10
26
93
CHC
512
1215
MALE
10
26
93
CHC
507
1110
FMALE
10
26
93
CHC
467
825
FMALE
10
13
93
LMB
405
1040
C
10
13
93
LMB
360
720
c
10
14
93
LMB
383
865
FMALE
10
22
93
LMB
402
1065
FMALE
10
22
93
LMB
412
1115
MALE
10
27
93
LMB
360
615
FMALE
10
27
93
LMB
380
780
FMALE
10
27
93
LMB
476
1540
FMALE
10
27
93
LMB
568
2775
FMALE
10
27
93
LMB
503
1750
FMALE
10
27
93
LMB
548
2750
MALE
10
27
93
LMB
378
675
FMALE
10
27
93
LMB
314
395
FMALE
10
27
93
LMB
323
470
MALE
10
27
93
LMB
318
400
FMALE
10
13
93
SBU
402
915
MALE
10
13
93
SBU
442
1365
MALE
10
13
93
SBU
520
2265
MALE
10
13
93
SBU
345
605
MALE
10
13
93
SBU
375
765
FMALE
10
13
93
SBU
397
975
FMALE
10
13
93
SBU
488
2245
MALE
10
13
93
SBU
430
1530
FMALE
10
14
93
SBU
532
2245
FMALE
10
14
93
SBU
468
1600
MALE
10
14
93
SBU
421
1275
MALE
10
12
93
SBU
485
1880
C
10
22
93
SBU
524
2195
MALE
10
22
93
SBU
564
2045
FMALE
10
22
93
SBU
495
1885
MALE
11
9
93
CHC
505
1280
C
11
9
93
CHC
490
1120
C
11
9
93
CHC
550
1480
c
11
9
93
CHC
440
760
c
11
22
93
CHC
596
2175
MALE
21
-------
Collection Site
Date
Species' Length (mm) Weight (g) Sex LABID"
TRM325
11
29
93
CHC
265
395
FMAI.F.
33025
TRM325
11
29
93
CHC
381
405
FMALE
33025
TRM325
12
2
93
CHC
376
420
MALE
33025
TRM 325
12
2
93
CHC
400
465
MALE
33025
TRM 325
12
2
93
CHC
395
560
MALE
33025
TRM325
12
2
93
CHC
395
450
MALE
33026
TRM325
12
2
93
CHC
362
395
FMALE
33026
TRM325
12
2
93
CHC
421
640
MALE
33026
TRM 325
12
2
93
CHC
458
710
MALE
33026
TRM325
12
2
93
CHC
480
1060
FMALE
33026
TRM 325
11
9
93
LMB
295
300
C
33012
TRM 325
11
9
93
LMB
398
880
C
33012
TRM 325
11
9
93
LMB
320
460
c
33012
TRM 325
11
9
93
LMB
380
760
c
33012
TRM 325
11
9
93
LMB
295
360
c
33012
TRM 325
11
9
93
LMB
375
760
c
33014
TRM 325
11
9
93
LMB
355
620
c
33014
TRM 325
11
9
93
LMB
310
400
c
33014
TRM 325
11
9
93
LMB
290
320
c
33014
TRM 325
11
9
93
LMB
295
300
c
33014
TRM 325
11
9
93
LMB
480
1620
c
33017
TRM 325
11
9
93
LMB
445
1120
c
33017
TRM 325
11
9
93
LMB
540
2120
c
33017
TRM 325
11
9
93
LMB
540
1660
c
33017
TRM 325
11
9
93
LMB
495
2100
33017
TRM 325
11
2
93
SBU
428
1285
MALE
33027
TRM 325
11
2
93
SBU
445
1280
MALE
33027
TRM 325
11
10
93
SBU
475
1500
C
33027
TRM 325
11
11
93
SBU
455
1655
MALE
33027
TRM 325
11
26
93
SBU
520
1625
MALE
33027
TRM 325
11
26
93
SBU
454
1575
MALE
33028
TRM 325
11
26
93
SBU
508
2275
MALE
33028
TRM 325
11
29
93
SBU
455
1690
MALE
33028
TRM 325
11
29
93
SBU
505
1890
MALE
33028
TRM 325
11
29
93
SBU
510
1695
MALE
33028
TRM 325
11
29
93
SBU
498
2155
MALE
33029
TRM 325
11
29
93
SBU
530
2485
MALE
33029
TRM 325
11
29
93
SBU
488
1765
MALE
33029
TRM 325
11
29
93
SBU
559
2620
MALE
33029
TRM 325
11
29
93
SBU
533
2455
FMALE
33029
a CHC = channel catfish, LMB = largemouth bass, SBU = smallmouth buffalo
b LABID = number assigned by TVA's Environmental Chemistry Laboratory. It is used to link laboratory analysis data with physical data
from fish.
c Preprocessed by the research group from the Smithsonian Institution. Sex of these fish were not determined.
22
-------
Table 5.3-2 Concentrations (ng/g) of organics in composite samples from Wheeler Reservoir,
1993.
Collection Site
Species*
LABID"
PCB
DDT
Chlordane
% Lipid
TRM308
CHC
32604
0.5
0.81
<0.01
5.6
TRM308
CHC
32606
0.5
0.66
0.01
6.0
TRM308
CHC
32609
0.3
0.55
0.01
6.3
TRM308
LMB
32610
0.3
2.0
0.01
3.0
TRM308
LMB
32611
0.2
0.47
<0.01
2.0
TRM308
LMB
32612
0.2
0.30
<0.01
1.1
TRM308
SBU
32613
0.3
0.79
0.01
7.2
TRM308
SBU
32614
0.3
1.1
0.01
5.3
TRM308
SBU
32615
0.3
1.2
0.01
5.9
TRM315
CHC
33003
0.4
1.3
<0.01
5.1
TRM315
CHC
33005
0.7
0.69
<0.01
6.3
TRM315
CHC
33008
0.6
1.7
<0.01
9.2
TRM315
LMB
33009
0.7
2.0
<0.01
0.8
TRM315
LMB
33010
0.3
9.5
<0.01
0.6
TRM315
LMB
33011
0.2
1.1
<0.01
0.9
TRM315
SBU
33021
0.3
0.37
0.01
5.0
TRM315
SBU
33022
0.4
0.68
0.03
11
TRM315
SBU
33023
0.5
0.88
0.06
7.2
TRM320
CHC
32618
0.6
1.5
0.03
8.1
TRM320
CHC
32619
0.6
0.91
0.03
8.0
TRM320
CHC
32620
0.7
2.8
0.02
5.5
TRM320
LMB
32621
0.9
2.5
0.03
3.7
TRM320
LMB
32623
0.7
1.3
0.01
1.4
TRM320
LMB
32626
0.5
0.91
<0.01
0.9
TRM320
SBU
32627
0.3
3.7
0:01
4.8
TRM320
SBU
32628
0.3
13
0.03
12
TRM320
SBU
32629
0.7
21
0.04
6.7
TRM325
CHC
33024
1.0
1.5
0.04
7.4
TRM325
CHC
33025
1.3
0.88
0.02
5.2
TRM325
CHC
33026
0.9
0.43
0.04
5.8
TRM325
LMB
33012
0.4
1.5
<0.01
1.6
TRM325
LMB
33014
0.5
1.1
<0.01
1.9
TRM325
LMB
33017
1.2
6.4
<0.01
2.5
TRM325
SBU
33027
1.0
7.2
0.01
6.0
TRM325
SBU
33028
0.6
4.0
0.02
8.1
TRM325
SBU
33029
1.5
14
0.04
9.3
a CHC = channel catfish, LMB = largemouth bass, SBU = smallmouth buffalo
b LABID = number assigned by TVA's Environmental Chemistry Laboratory. It is used to link laboratory analysis data with physical data
from fish.
23
-------
Table 5.3-3 Summary of weight, length, and percent lipid content in catfish, largemouth bass and smallmouth buffalo from Wheeler
Reservoir, 1991-1993.
Channel Catfish
Largemouth Bass
Smallmouth Buffalo
TRM 308
TRM 315
TRM 320
TRM 325
TRM 308
TRM 315
TRM 320
TRM 325
TRM 308
TRM 315
TRM 320
TRM 325
1991
Weight Range
322-3170
288-3262
486-3240
580-4280
222-2260
292-1550
402-1636
400-2542
902-2374
682-2932
776-3662
802-4294
Mean Weight
1338
1859
1521
1811
703
693
1121
1032
1807
1698
1951
1949
Length Range
350-660
317-621
412-623
393-669
270-530
290-470
311-502
309-536
410-555
355-560
376-588
375-670
Mean Length
492
491
508
530
349
355
386
397
487
469
487
486
Number of Fish
15
15
15
15
15
15
15
15
15
15
15
15
% Lipid Range"
9.5-11.0
6.0-11.0
5.9-16.0
5.1-9.7
0.6-2.3
0 6-2.0
1.2-2.1
1.9-2.6
6.4-8.0
3.0-5.3
5.0-6.4
5.0-9.9
Mean % Lipid
10.5
8.7
9.7
8.1
1.4
1.3
1.7
2.2
7.1
4.2
5.7
6.7
Number of Composites
3
3
3
3
3
3
3
3
3
3
3
3
1992"
Weight Range
300-2470
615-1345
365-890
660-1415
300-2955
320-1630
360-3380
335-2350
695-2775
1005-3020
810-2100
1135-4000
Mean Weight
1198
958
643
962
1203
914
1166
942
1573
1616
1404
1796
Length Range
319-617
433-541
350-477
432-545
282-547
300-465
300-570
294-525
363-576
410-586
380-500
406-606
Mean Length
484
479
421
470
405
385
404
387
457
469
452
481
Number of Fish
15
12
3
9
15
15
15
15
15
15
15
15
% Lipid Range"
5.0-6.8
5.1-6.8
6
3.6-5.3
1.0-3.1
1.1-2.6
0.7-2.9
1.7-2.5
6.2-7.8
4.4-6.7
4.5-6.9
4.0-7.1
Mean % Lipid
5.8
5.9
4.5
1.8
1.9
1.7
2.1
6.9
5.2
5.3
5.2
Number of Composites
3
3
1
2
3
3
3
3
3
3
3
3
1993
Weight Range
595-1700
710--2370
665-1735
385-2175
330-2285
345-1045
395-2775
300-2120
1290-3030
465-3040
605-2265
1280-2620
Mean Weight
1115
1307
1256
820
659
629
1130
918
2153
1607
1587
1763
Length Range
421-525
434-586
440-583
265-596
305-516
306-408
314-568
290-540
431-553
328-557
345-532
428-559
Mean Length
472
500
528
434
351
355
409
387
504
453
455
459
Number of Fish
15
15
15
15
15
15
15
15
15
15
15
15
% Lipid Range'
5.6-6.3
5.1-9.2
5.5-8 1
5.2-7.4
1.1-30
0.6-0.9
0.9-3.7
1.6-2.5
5.3-7.2
5.0-11
4.8-12
6.0-8.1
Mean % Lipid
6.0
6.9
7.2
6.1
2.0
0.8
2.0
2.0
6.1
7.7
7.8
7.1
Number of Composites
3
3
3
3
3
3
3
3
3
3
3
3
a The values listed as "% Lipid Range" correspond to the lipid content of composites,
b Actually collected in January 1993.
2A
-------
Table 5.3-4 Two-way analysis of variance (location and year main effects) and
Ryan-Einot-Gabriel-Welsch Multiple Range Test on lipid content and total weight
in catfish, largemouth bass, and smallmouth buffalo from Wheeler Reservoir,
1991-1993.
Variable
Source of
Variation
P>F
REGW Multiple Range Test"
Mean Rank Low to High
Lipid content
Location
Year
Interaction
CATFISH
0.5764
0.0031
0.9316
1992 1993 1991
Total Weight
Location
Year
Interaction
0.7446
0.0016
0.0102
Significant Interaction
Lipid content
LARGEMOUTH BASS
Location
Year
Interaction
0.1984
0.8201
0.6036
No
Significant
Difference
Total Weight
Location
Year
Interaction
0.0716
0.0815
0.4131
No
Significant
Difference
SMALLMOUTH BUFFALO
Lipid content
Location
Year
Interaction
0.5539
0.8739
0.4024
No
Significant
Difference
Total Weight
Location
Year
Interaction
0.1648
0.0926
0.2411
No
Significant
Difference
Years or locations underscored by the same lines were not significantly different at a = 0.05.
Years and locations not so underscored were significantly different.
25
-------
Table 5.3-5 One-way analysis of variance and Ryan-Einot-Gabriel-Welsch Multiple Range Test
on total weight in channel catfish collected from Wheeler Reservoir, 1991-1993.
REGW Multiple Range Test"
Year/Location Variable P>F Mean Rank Low to High
1993
Location
0.0013
325 308 320 315
308
Year
0.8657
No Significant Difference
315
Year
0.2665
No Significant Difference
320
Year
0.0404
1992" 1993 1991
325
Year
0.0007
1993 1992" 1991
a Years or locations underscored by the same lines were not significantly different at a = 0.05.
Years and locations not so underscored were significantly different,
b Actually collected in January 1993.
26
-------
Table 5.3-6 Summary of total PCB concentrations (ng/g) in catfish, largemouth bass and smallmouth buffalo composites"
from Wheeler Reservoir, 1991 -1993.
Channel Catfish
Largemouth Bass
Smallmouth Buffalo
TRM 308
TRM 315
TRM 320
TRM 325
TRM 308
TRM 315
TRM 320
TRM 325
TRM 308
TRM 315
TRM 320
TRM 325
1991
Range
1.0-1.6
0.9-1.7
1.3-1.6
0.9-1.3
0.1-0.3
0 1-0.2
0.5-2.3
0.1-0.6
0.2-0.2
0.3-0.6
0.8-1.2
0.4-0.6
Mean
1.3
1.3
1.5
1.1
0.2
0.1
1.4
0.3
0.2
0.5
1.0
0.5
Number > 2 Opg/g
0
0
0
0
0
0
1
0
0
0
0
0
Number of composites'
3
3
3
3
3
3
3
3
3
3
3
3
1992'
Range
0.2-0.7
0.9-1.1
0.6
0.8-0.9
0.1-0.7
0.1-0.9
0.3-0.5
0.3-0.5
0.2-0.3
0.3-0.7
0.3-0.5
0.6-0.9
Mean
0.5
1.0
0.9
0.3
0.6
0.4
0.4
0.3
0.5
0.4
0.7
Number > 2.0ng/g
0
0
0
0
0
0
0
0
0
0
0
Number of composites*
3
3
1
2
3
3
3
3
3
3
3
3
1993
Range
0.5-0.3
0.6-0.7
0.6-0.9
0.9-1.3
0.2-0.4
0.2-0.3
0.3-0.7
0.4-1.2
0.3-0.4
0.4-0.6
0.3-1.0
0.6-1.5
Mean
0.4
0.7
0.7
1.1
0.3
0.3
0.5
0.7
0.3
0.5
0.6
1.0
Number > 2.0pg/g
0
0
0
0
0
0
0
0
0
0
0
0
Number of composites'
3
3
3
3
3
3
3
3
3
3
3
3
a Catfish, largemouth bass, and smallmouth buffalo were analyzed as five-fish composites using methods similar to screening studies. The values listed as "Number of composites" correspond to the
number of five-fish composites from a particular location in a particular year,
b Actually collected in January 1993
27
-------
Table 5.3-7 Summary of total DDT concentrations (ng/g) in catfish, largemouth bass and smallmouth buffalo composites"
from Wheeler Reservoir, 1991-1993.
Channel Catfish
Largemouth Bass
Smallmouth Buffalo
TRM 308
TRM 315
TRM 320
TRM 325
TRM 308
TRM 315
TRM 320
TRM 325
TRM 308
TRM 315
TRM 320
TRM 325
1991
Range
5.7-13
1.9-7.8
6.1-13
1.1-2.8
0.49-1.2
2.6-3.3
5.0-11
0.12-11
1.7-2.9
2.3-8.5
18-43
2.0-5.5
Mean
8.4
4.3
9.4
2.2
0.89
3.4
7.4
4.3
2.4
5.2
27
3.5
Number of composites"
3
3
3
3
3
3
3
3
3
3
3
3
1992"
Range
0.63-3.1
2.0-2.3
1.6
0.60-0.72
0.34-2.6
0.52-7.4
1.5-1.9
1.3-2 4
1.1-1.5
2.3-9.2
2.7-5.0
0.94-9.2
Mean
2
2.2
0.66
1.2
5.1
1.7
2
1.3
4.7
3.7
3.9
Number of composites'
3
3
1
2
3
3
3
3
3
3
3
3
1993
Range
0.55-0.81
0.69-1.7
0.91-2.8
0.43-1.5
0.30-2.0
0.53-2.0
0.91-2.5
1.1-6.4
0.79-1.2
0.37-0.88
3.7-21
4.0-14
Mean
0.67
1.2
1 7
0.94
0.92
1.2
1.6
3.0
1.0
0.64
13
8.4
Number of composites'
3
3
3
3
3
3
3
3
3
3
3
3
a Catfish, largemouth bass, and smallmouth buffalo were analyzed as five-fish composites using methods similar to screening studies. The values listed as "Number of composites" correspond to the
number of five-fish composites from a particular location in a particular year.
b Actually collected in January 1993
28
-------
Table 5.3-8 Two-way analysis of variance (location and year main effects) and
Ryan-Einot-Gabriel-Welsch Multiple Range Test on PCB and DDT
concentrations in catfish, largemouth bass, and smallmouth buffalo
from Wheeler Reservoir, 1991-1993.
PCB Location
Year
Interaction
REGW Multiple Range Test*
P>F Mean Rank Low to High
CATFISH
0.0159
0.0001
0.0220 Significant Interaction
DDT Location 0.0104 325 315 308 320
Year 0.0001 1993 1992 1991
Interaction 0.0698
LARGEMOUTH BASS
PCB Location 0.0162
Year 0.9818
Interaction 0.0235 Significant Interaction
DDT
Location 0.0589
Year 0.1414
Interaction 0.3117
No
Significant
Difference
SMALLMOUTH BUFFALO
PCB Location 0.0001
Year 0.1281
Interaction 0.0167 Significant Interaction
DDT Location 0.0001
Year 0.0146
Interaction 0.0034 Significant Interaction
Years or locations underscored by the same lines were not significantly different at a = 0.05.
Years and locations not so underscored were significantly different.
29
-------
Table 5.3-9 One-way analysis of variance (location effects) and Ryan-Einot-
Gabriel-Welsch Multiple Range Test on PCB and DDT concentrations
in channel catfish, largemouth bass and smallmouth buffalo from
Wheeler Reservoir, 1993.
REGW Multiple Range Test3
Analyte P>F Mean Rank Low to High
Channel Catfish
PCB Location 0.0037 308 315 320 325
DDT Location 0.2396 No Significant Difference
Largemouth Bass
PCB Location 0.0972 No Significant Difference
DDT Location 0.4553 No Significant Difference
Smallmouth Buffalo
PCB Location 0.0732 No Significant Difference
DDT Location 0.0024 315 308 325 320
a Years or locations underscored by the same lines were not significantly different at a = 0.05.
Years and locations not so underscored were significantly different.
30
-------
Table 5.3-10 One-way analysis of variance (year effects) and Ryan-Einot-Gabriel-
Welsch Multiple Range Test on PCB concentrations among years for
each location in channel catfish, largemouth bass, and smallmouth
buffalo from Wheeler Reservoir, 1991 -1993.
Location
P>F
REGW Multiple Range Test"
Mean Rank Low to High
Channel Catfish
308
0.0131
1993 1992b 1991
315
0.0327
1993 1992b 1991
320
0.0075
1992 1993 1991
325
0.3491
No Significant Difference
Largemouth Bass
308
0.8944
No Significant Difference
315
0.1792
No Significant Difference
320
0.0959
No Significant Difference
325
0.2870
No Significant Difference
Smallmouth Buffalo
308
0.0344
1991 1992b 1993
315
0.9433
No Significant Difference
320
0.0627
No Significant Difference
325
0.1278
No Significant Difference
Years or locations underscored by the same lines were not significantly different at d = 0.05.
Years and locations not so underscored were significantly different
Actually collected in January 1993.
31
-------
Table 5.3-11 One-way analysis of variance (year effects) and Ryan-Einot-Gabriel-
Welsch Multiple Range Test on DDT concentrations in smallmouth
buffalo from Wheeler Reservoir, 1991-1993.
REGW Multiple Range Test8
Location
P>F
Mean Rank Low to High
308
Year
0.0139
1993 1992b
1991
315
Year
0.0376
1993 1992
1991
320
Year
0.0220
1992 1993
1991
325
Year
0.3132
No Significant Difference
a Years or locations underscored by the same lines were not significantly different at a = 0.05.
Years and locations not so underscored were significantly different,
b Actually collected in January 1993.
32
-------
Table 5.3-12 DDT concentrations (ng/g wet weight) in composites of channel catfish, largemouth bass, and smallmouth
buffalo from Wheeler Reservoir, 1991-1993.
TRM308
TRM315
TRM320
TRM325
1991'
1992°
1993°
1991
1992
1993
1991.
1992
1993
1991
1992
1993
Channel Catfish
1-5
13
3.1
0.81
3.3
2.0
1.3
13
1.6
1.5
2.8
0.60
1.5
6-10
6.7
2.3
0.66
1.9
2.2
0.69
8.8
0.91
2.6
0.72
0.88
11-15
5J_
0.63
0.55
11
21
LI
6J.
IA
LL
0.43
Mean
8.4
2.0
0.67
4.3
2.2
1.2
9.4
1.7
2.2
0.66
0.95
Smallmouth Buffalo
1-5
1.6
1.1
0.79
4.6
2.6
0.37
18
5.0
3.7
5.5
9.2
7.2
6-10
2.7
1.2
1.1
2.3
9.2
0.68
20
3.4
13
3.1
0.9
4.0
11-15
2^9
LI
12
M
23
0.88
43
2J_
21
2.0
LI
14
Mean
2.4
1.3
1.0
5.1
4.7
0.64
27
3.7
13
3.5
3.7
8.4
Larpemouth Bass
1-5
1.1
2.6
2.0
2.6
7.4
2.0
4.9
1.9
2.5
11
2.4
1.5
6-10
1.0
0.55
0.47
4.3
7.4
0.53
6.6
1.5
1.3
1.6
2.3
1.1
11-15
01
0.34
03
3J_
05
U
11
L8
0.91
OJ.
LI
M
Mean
0.9
1.2
0.92
3.3
5.0
1.2
7.4
1.7
1.6
4.3
2.0
3.0
a 1991 = October 1991; 1992 = January 1993; 1993 = October-November 1993
33
-------
Chapter 6
Guntersville Reservoir-
Sequatchie River Watershed
SEORM 7.1
Mercury concentration (0.63 ng/g) in lone spotted bass was
sufficiently hi^h to warrant resampling in summer 1995.
TN
Nickajack Reservoir-
Chickamauga Reservoir
Watershed
Wheeler Reservoir Watershed
AL
At
\
GA
\
\
^ Stream Monitoring Sites sampled in 1993
£ Stream Monitoring Sites not sampled in 1993
^ Reservoir Monitoring Sites sampled in 1993
O Reservoir Monitoring Sites not sampled in 1993
34
-------
6.0 Guntersville Reservoir-Seguatchie River Watershed
6.1 Introduction
Fish for fish tissue screening studies were collected from only one site in the Guntersville
Reservoir-Sequatchie River Watershed in 1993, a stream monitoring site at Sequatchie River Mile
(SEQRM) 7.1. Publications containing historical data from monitoring sites within the
Guntersville Reservoir- Sequatchie River Watershed are in Appendix B.
6.2 Methods
A composite of five channel catfish was collected from the stream monitoring site along
with one largemouth bass and one spotted bass. These fish were analyzed for lipids, PCBs,
pesticides and selected metals on the EPA Priority Pollutant List according to the methods for
screening studies in Appendix C.
6.3 Results and Recommendations
Physical information and results from the chemical analyses for these fish are contained in
Appendix A along with data from other stream and reservoir monitoring sites. Mercury
concentration (0.63 |ig/g) in the single spotted bass from SEQRM 7.1 was the only analyte to
exceed Tier 2 levels. Elevated mercury concentrations had not been found in previous years.
This station is part of the newly implemented two-year rotation for streams and will be sampled in
summer 1995.
35
-------
Chapter 7
Nickajack Reservoir-
Chickamauga Reservoip
Watershed
Walls Bar Reservoir-
Fort Loudoun Reservoir-
Mehon Hill Reservoir Watersheds
Guntersville Reservoir-
Sequatchie River Watershed
a Reservoir Monitoring Sites sampled in 1993
O Reservoir Monitoring Sites not sampled in 1993
A Stream Monitoring Sites sampled in 1993
A Stream Monitoring Sites not sampled in 1993
^jTrend Study Sites sampled in 1993
PlTreod Study Sites not sampled in 1993
4- DOE Clinch River Environmental Restoration Project
36
-------
Chapter 7.0 Chickamauga Reservoir - Nickaiack Reservoir Watershed
7.1 Introduction
In 1989, the Tennessee Department of Environment and Conservation (TDEC) issued a
precautionary advisory suggesting, "that children, pregnant women, and nursing mothers avoid
eating catfish from Nickajack Reservoir and that others persons limit their consumption of catfish
to 1.2 pounds per week." The most current fish consumption advisory from TDEC is Appendix
D.
Fish tissue samples were collected at four locations in the Chickamauga Reservoir -
Nickajack Reservoir Watershed in 1993. Three of these locations (TRMs 425, 457, and 469)
were within Nickajack Reservoir and were part of a long-term trend study on PCBs and
chlordane. The other location was in Watts Bar Dam tailwater and fish were collected as part of a
contract with DOE for their Clinch River Environmental Restoration Project (CRERP). Data
from the fish collected in 1993 for the CRERP were no available at the time this report was
written. Historical data from monitoring sites within the Chickamauga Reservoir - Nickajack
Reservoir Watershed are available in publications listed in Appendix B.
7.2 Nickajack Trend Analysis Study
Results of the Valley-wide Fish Tissue Screening Study in 1987 found sufficiently high
concentrations of both PCBs and chlordane in channel catfish (the indicator species) from
Nickajack Reservoir to warrant further investigation. PCB concentrations exceeded the
37
-------
predetermined Tier 3 levels (Table 1-1) established to trigger more in-depth studies to better
define apparent problems. The five-catfish fillet composite sample from the lower reservoir
location (TRM 425) contained 1.9 (ig/g PCBs and 0.21 jxg/g chlordane, while the composite
sample from the upper area (TRM 457) contained 1.3 (ig/g PCBs and 0.25 ng/g chlordane
(Dycus 1989a).
Follow-up studies were conducted in autumn 1988, 1989, 1990, 1991, 1992, and 1993 to
further define the temporal trend of PCB and chlordane contamination in Nickajack Reservoir
catfish and to investigate concentrations in other important species. The results of the 1993 study
are presented in this report as well as comparisons among catfish for the six years of data
(1988-1993).
Methods
Ten channel catfish and ten carp were collected from TRMs 425 and 457 in 1993. Ten
striped bass were collected from TRM 469. These fish were analyzed individually for lipids,
PCBs, and chlordane. All procedures involved in field sampling, processing, and laboratory and
data analysis were similar to those described in Appendix C and will not be repeated here.
Results and Recommendations
Physical information and the results of analyses are presented in Tables 7.2-1 through
7.2-8. The two-way ANOVA on channel catfish weights with location and year as the two main
effects had a significant interaction term, primarily because quite small fish were collected at TRM
457 in 1989. A one-way ANOVA on weight of catfish collected in 1993 failed to detect a
38
-------
significant difference between TRMs 425 and 457. Lipid content of catfish was not significantly
different among years or locations.
PCB concentrations in channel catfish were slightly higher in 1993 (mean at TRMs 425
and 457 was 0.6 and 0.7 ng/g, respectively) than in 1992, but still lower than in previous years.
Statistical analyses indicated concentrations in 1992 and 1993 were significantly lower than in
previous years. PCB concentrations were not significantly related to either total weight or lipid
content.
Total weight of individual carp was significantly lower and lipid content significantly
higher in 1991 than in 1992 and 1993. The two-way ANOVA on PCB concentrations in carp had
a significant interaction term, primarily because PCB concentrations in carp have been consistent
at TRM 425 ( mean concentrations = 0.3 ng/g in 1991, 1992, and 1993) but inconsistent at TRM
457 (mean PCB concentrations = 1.2 ng/g in 1991, 0.3 ng/g in 1992, and 0.7 |ig/g in 1993).
PCB concentrations in 1993 were significantly higher at TRM 457 than 425.
Striped bass from TRM 469 weighed significantly more in 1993 than in 1992, but lipid
content and PCB concentrations were not significantly different. PCB concentrations in striped
bass have been higher than in channel catfish in both 1992 and 1993.
Further examination of striped bass is warranted because concentrations in 1992 and 1993
were near the level used by TDEC to issue a "limit-consumption" advisory. Also, channel catfish
should be sampled again in 1994 to determine if the lower concentration of PCBs seen in 1992
and 1993 continue, possibly leading to altering the advisory. Carp would not be sampled unless
TDEC recognizes a specific need.
39
-------
Table 7.2-1 Physical data and analyte concentrations (ng/g) in carp, channel catfish, and striped
bass from Nickajack Reservoir, 1993.
Collection Site
Species'
Length (mm) Weight (g)
Sex
LABID"
%LIPIDS
PCB
Chlordane
TRM425
C
610
3461
MALE
32916
9.1
0.3
0.01
TRM425
C
569
2602
MALE
32918
6.9
0.2
<0.01
TRM425
C
624
3701
MALE
32921
6.4
0.2
<0.01
TRM425
c
695
6881
FMALE
32923
8.7
0.4
0.02
TRM425
c
694
5146
MALE
32926
8.7
0.4
0.02
TRM425
c
696
4994
FMALE
32928
3.5
0.2
<0.01
TRM425
c
746
6516
MALE
32931
6.4
0.4
<0.01
TRM425
c
760
6223
FMALE
32932
5.8
0.4
<0.01
TRM425
c
751
6507
FMALE
32933
8.0
0.6
<0.01
TRM425
c
748
6345
FMALE
32934
4.6
0.3
<0.01
TRM425
CHC
590
2359
FMALE
32906
3.7
0.4
0.01
TRM425
CHC
481
1071
MALE
32907
13
0.8
0.03
TRM425
CHC
517
1436
Ic
32908
6.0
0.5
0.01
TRM425
CHC
556
1370
FMALE
32909
4.8
1.0
0.03
TRM425
CHC
475
989
FMALE
32910
6.6
0.3
0.01
TRM425
CHC
470
921
Ic
32911
10
0.7
0.02
TRM425
CHC
496
1069
MALE
32912
5.8
0.3
<0.01
TRM425
CHC
422
650
MALE
32913
1.8
0.4
0.01
TRM425
CHC
595
2226
FMALE
32914
5.4
0.7
<0.01
TRM425
CHC
460
836
FMALE
32915
11
0.8
0.02
TRM457
CHC
470
1060
MALE
32935
9.6
0.6
<0.01
TRM457
CHC
419
714
FMALE
32936
5.9-
0.9
<0.01
TRM457
CHC
432
869
FMALE
32939
6.9
0.7
0.01
TRM457
CHC
575
2141
MALE
32940
13
1.0
0.01
TRM457
CHC
529
1653
FMALE
32941
14
1.2
<0.01
TRM457
CHC
536
1540
MALE
32942
8.3
0.7
<0.01
TRM457
CHC
412
663
FMALE
32943
6.4
0.3
<0.01
TRM457
CHC
461
945
FMALE
32944
3.7
0.3
<0.01
TRM457
CHC
570
1939
FMALE
32945
3.8
0.6
<0.01
TRM457
CHC
476
1061
MALE
32946
90
0.7
0.01
40
-------
Collection Site
Species3
Length (mm) Weight (g)
Sex
LABIDb
%LIPIDS
PCB
Chlordane
TRM457
C
713
5147
MALE
32947
4.9
1.8
<0.01
TRM457
c
701
6547
MALE
32949
3.1
0.5
<0.01
TRM457
c
671
4298
MALE
32952
3.6
0.5
<0.01
TRM457
c
710
4692
MALE
32954
10
0.6
<0.01
TRM457
c
655
3768
MALE
32960
6.0
0.4
0.02
TRM457
c
695
4603
MALE
32962
2.9
0.6
0.02
TRM457
c
747
5672
MALE
32965
5.4
0.9
0.12
TRM457
c
715
5071
MALE
32967
3.2
0.5
0.05
TRM457
c
750
5559
MALE
32970
7.5
0.8
0.21
TRM457
c
687
4362
MALE
32972
6.2
0.7
0.10
TRM469
STB
542
1618
FMALE
32975
5.3
0.6
0.06
TRM469
STB
685
3388
FMALE
32976
8.2
0.8
0.03
TRM469
STB
698
3953
MALE
32977
13
1.2
0.11
TRM469
STB
706
4268
FMALE
32978
9.9
0.8
0.05
TRM469
STB
700
3856
FMALE
32981
6.5
1.0
0.03
TRM469
STB
768
6513
FMALE
32983
9.1
0.8
0.04
TRM469
STB
700
3929
FMALE
32986
8.2
0.8
0.03
TRM469
STB
724
3823
FMALE
32987
5.6
0.9
0.04
TRM 469
STB
749
4925
FMALE
32988
10
0.7
<0.01
TRM469
STB
850
7324
MALE
32989
7.0
1.9
0.13
a CHC = channel catfish, C = carp, STB = striped bass
b LAB ID = number assigned by TVA's Environmental Chemistry Laboratory. It is used to link laboratory
analysis data with physical data from fish.
c I = immature (sex could not be determined).
41
-------
Table 7.2-2 Summary of lengths, total weights, and percent lipids of catfish, carp, and striped bass from Nickajack Reservoir,
collected from 1988 to 1993.
Weight Range Mean Weight Length Range Mean Length % Lipid Range Mean % Lipid
1988 Catfish TRM 425
1835-2705
2175
555-650
587
0.9-18.0
11.4
TRM 457
1198-2340
1854
472-602
540
8.9-20.0
13.6
1989 Catfish TRM 425
346-1798
1048
331-565
458
3.0-20.0
10.3
TRM 457
308-1001
805
332-470
397
3.2-17.0
10.9
1990 Catilsh TRM 425
464-2332
1215
370-596
484
5.4-20 0
10.7
TRM 457
736-2429
1500
426-656
528
3.6-24 0
12.4
1991 Catfish TRM 425
570-2512
1607
395-597
521
4.8-14.0
8.1
TRM 457
962-2839
2100
451-625
565
0.1-27 0
14.1
Carp TRM 425
1602-5017
3350
477-725
617
4.0-16.0
10.1
TRM 457
3522-7932
4958
633-780
686
3.9-14.0
9.4
1992 Catfish TRM 425
762-1845
1144
446-585
497
2.3-12.0
7.3
TRM 457
883-2620
1453
463-610
516
2.3-20.0
10 1
Carp TRM 425
3460-8414
5150
633-846
708
2.6-12.0
6.2
TRM 457
3635-8943
6552
646-799
749
3.5-12.0
6.5
Striped Bass TRM 470
1619-3311
2305
494-686
594
7 3-12.0
9.1
1993 Catfish TRM 425
650-2359
1293
422-595
506
1.8-13.0
6.8
TRM 457
663-2141
1259
412-575
488
3.7-14.0
8.1
Carp TRM 425
2602-6881
5238
569-760
689
3.5-9.1
6.8
TRM 457
3768-6547
4972
655-750
704
2.9-10.0
5.3
Striped Bass TRM 469
1618-7324
4360
542-850
712
5.3-13.0
8.3
42
-------
Table 7.2-3 Two-way analysis of variance (location and year main effects) and Ryan-Einot-
Gabriel-Welsch Multiple Range Test on lipid content and total weight in catfish
and carp from Nickajack Reservoir, 1988-1993.
Variable
Source of
Variation
P>F
REGW Multiple Range Test'
Mean Rank Low to High
Lipid content
Location
Year
Interaction
CATFISH
0.0573
0.1160
0.8646
No
Significant
Difference
Total Weight
Location
Year
Interaction
0.9384
0.0001
0.0090
Significant Interaction
Lipid content
Location
Year
Interaction
CARP
0.4305
0.0006
0.5315
1993 1992 1991
Total Weight
Location
Year
Interaction
0.0049
0.0008
0.0602
425 ,457
1991 1993 1992
a Years underscored by the same lines were not significantly different at a = 0.05.
Years not so underscored were significantly different.
43
-------
Table 7.2-4 One-way analysis of variance and Ryan-Einot-Gabriel-Welsch Multiple Range Test
on total weight in channel catfish from Nickajack Reservoir, 1988-1993.
REGW Multiple Range Test"
Fixed Variable P>F Mean Rank Low to High
1993 Location 0.8993 No Significant Difference
425 Year 0.0008 1989 1992 1990 1993 1991 1988
457 Year 0.0001 1989 1993 1992 1990 1988 1991
a Years underscored by the same lines were not significantly different at a = 0.05.
Years not so underscored were significantly different.
44
-------
Table 7.2-5 Summary of total PCB concentrations (|ig/g) in individual catfish, carp,
smallmouth buffalo, and striped bass fillets from Nickajack Reservoir, collected
from 1988 to 1992.
Catfish Carp Smallmouth Buffalo Striped Bass
TRM425 TRM 457 TRM 425 TRM 457 TRM 425 TRM 457 TRM 470
1988'
Range
0.4-1.9
0.9-1.7
Mean
0.9
1.3
Number > 2.0\ig/g
0
0
Number offish
10
3
1989
Range
0.6-2.0
0 6-2.0
Mean
1.3
0.7
Number > 2.0(ig/g
1
1
Number of fish
10
10
1990
Range
0.6-1.5
0.4-1.7
Mean
1.0
1.1
Number > 2.0|ig/g
0
0
Number offish
10
10
1991
Range
0.3-3.6
0.2-1.9
0.1-0.8
0.3-2.7
0.1-0.7 0.1-0.
Mean
1.5
0.9
0.3
1.2
0.2 0.4
Number > 2.0fjg/g
2
0
0
1
0 0
Number of fish
10
10
10
9
10 4
1992
Range
0.1-0.8
0.1-0.8
0.1-0.7
0.1-0.6
Mean
0.4
0.5
0.3
0.3
Number > 2.0ng/g
0
0
0
0
Number offish
10
10
10
9
1993
Range
0.3-1.0
0.3-1.2
0.2-0.6
0.4-1.8
Mean
0.6
0.7
0.3
0.7
Number > 2.0fig/g
0
0
0
0
Number of fish
10
10
10
10
a Catfish collected in January and February 1989.
45
-------
Table 7.2-6 Two-way analysis of variance3 (location and year main effects) and Ryan-Einot-
Gabriel-Welsch Multiple Range test on PCB concentrations in catfish and carp
from Nickajack Reservoir, 1988-1993.
P>F
REGW Multiple Range Testb
Mean Rank Low to High
Catfish
Location
Year
Interaction
0.7155
0.0001
0.0725
1992 1993 1990 1988 1991 1989
Carp
Location
Year
Interaction
0.0001
0.0011
0.0018
Significant Interaction
a Preliminary test indicated PCB concentrations in catfish and carp were not related to lipid
content or weight, hence, ANOVA was the appropriate test
b Years or locations underscored by the same lines were not significantly different at a = 0.05.
Years and locations not so underscored were significantly different.
46
-------
Table 7.2-7 One-way analysis of variance and Ryan-Einot-Gabriel-Welsch Multiple Range test
on PCB concentrations in carp from Nickajack Reservoir, 1991-1993.
REGW Multiple Range Test3
Year/Location Variable P>F Mean Rank Low to High
1993 Location 0.0021 425 457
425 Year 0.6300 No Significant Difference
457 Year 0.0013 1992 1993 1991
a Years underscored by the same lines were not significantly different at a = 0.05.
Years not so underscored were significantly different.
47
-------
Table 7.2-8 One-way analysis of variance (year effects) and Ryan-Einot-Gabriel-Welsch
Multiple Range test on lipid content, total weight, and PCB concentrations in
striped bass from TRM 469, Nickajack Reservoir, 1992-1993.
REGW Multiple Range Testb
P>F Mean Rank Low to High
Lipid Year 0.3623 No Significant Difference
Weight Year 0.0362 1992 1993
PCB Year 0.2064 No Significant Difference
a Preliminary test indicated PCB concentrations in striped bass were not related to lipid content or weight,
hence, ANOVA was the appropriate test
b Years underscored by the same lines were not significantly different at a = 0.05.
Years not so underscored were significantly different.
48
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/
Nickajack Reservoir-
Chickamauga Reservoir
Watershed
A Stream Monitoring Sites sampled in 1993
A Stream Monitoring Sites not sampled in 1993
• Reservoir Monitoring Sites sampled in 1993
O Reservoir Monitoring Sites not sampled in 1993
Chapter 8
Hiwassee River Watershed
-------
8.0 Hiwassee River Watershed
8.1 Introduction
Fish tissue samples were collected at one stream monitoring site and seven reservoir
monitoring sites in the Hiwassee River Watershed in 1993. The stream monitoring site was
located at Hiwassee River mile (HiRM) 38. Three of the seven reservoir monitoring sites were in
the forebays of Chatuge Reservoir (HiRM 122),- Nottely Reservoir (Nottely River Mile (NRM)
24), and Blue Ridge Reservoir (Toccoa River Mile (ToRM) 54). The other four reservoir
monitoring sites were in the forebays and transition zones of Hiwassee Reservoir (HiRMs 77 and
85) and Ocoee #1 (Ocoee River mile (ORM) 12 and mouth of Sylco Creek embayment (ORM
16). The sites in Hiwassee, Chatuge, Nottely, and Blue Ridge Reservoirs were sampled to
examine mercury levels in tributary reservoirs. The samples from Ocoee #1 Reservoir were a
continuation of a study of PCBs.
Screening studies in Ocoee #1 Reservoir in 1987 had indicated relatively high PCB
concentrations (> 1.0 ng/g). Additional screening samples in 1988, 1989, 1990, and 1991 found
similar levels. A more detailed study in autumn 1992 confirmed an average PCB concentration in
channel catfish of 1.0-1.5 ng/g. A final decision about issuing an advisory had not been made by
TDEC at the time sample collection was planned for autumn 1993. As a result, samples were
collected at the screening level to continue the database for this reservoir. Final decision on
issuance of an advisory had not been made at the time this report was prepared. Historical data
from monitoring sites within the Hiwassee River Watershed are available in publications listed in
Appendix B.
50
-------
8.2 Methods
Five channel catfish and largemouth bass were collected from the stream monitoring site at
HiRM 38. Five channel catfish were collected from the seven reservoir monitoring sites. These
fish were analyzed as composites for lipids, pesticides, PCBs, and selected metals on the EPA
Priority Pollutant List.
Five largemouth bass were collected from HiRMs 85 and 122, NRM 24, and ToRM 54.
Four largemouth bass were collected from HiRM 77. These bass were analyzed as composites for
mercury only. In addition to complete analysis, many largemouth bass weighing more than 1200
grams were analyzed individually in an attempt to describe worse-case conditions. Further, all
largemouth bass, regaurdless of size, from Hiwassee Reservoir were analyzed individually.
Results of mercury analyses are in Appendix F. Field handling and processing and laboratory
processing were performed according to the methods for screening studies outlined in Appendix
C.
8.3 Results and Recommendations
Physical information and the results of metals and organics analyses for the stream and
reservoir monitoring sites are included in Appendix A. Results of mercury analyses on
largemouth bass are in Appendix F. PCB concentrations in channel catfish from the forebay (0.8
Hg/g) and upper region (1.0 ng/g) of Ocoee #1 and mercury concentrations in channel catfish
from the forebays of Hiwassee (0.54 ng/g) and Nottley Reservoirs (0.60 ng/g) were the only
analytes from the Hiwassee River Watershed to approach or exceed Tier 2 levels. Mercury
51
-------
results from individual, large largemouth bass were also near the 0.5 ng/g level, possibly
indicating need for further investigation (Appendix F).
Continued sampling of channel catfish from Ocoee #1 is needed because PCB
concentrations continue to be near the level used by TDEC to issue a precautionary advisory.
Implications of the relatively high mercury concentrations were still under consideration when this
report was prepared. It is likely that further investigation of this possible concern is warranted.
52
-------
Chap
Clinch River-Powell River Watershed
Watts Bar Reservoir-Fort Loudoun Reservoir
Melton Hill Reservoir Watershed
~ Stream Monitoring Sites sampled in 1993
A Stream Monitoring Sites not sampled in 1993
H Trend Study Sites sampled in 1993
I I Trend Study Sites not sampled in 1993
+ DOE Clinch River Environmental Restoration Proje
Three Embayment Sites sampled in 1993
French Broad River Watershed
Nickajack Reservoir-
Chickamauga Reservoir
Watershed
-------
Chapter 9.0 Watts Bar Reservoir - Fort Loudoun Reservoir - Melton Hill Reservoir Watershed
9.1 Introduction
The Tennessee Department of Environment and Conservation (TDEC) has issued
advisories against consuming certain fish from all three reservoirs in this watershed, Watts Bar,
Melton Hill, and Fort Loudoun. The most current advisory is Appendix D.
Fish tissue samples were collected at eighteen locations in the Watts Bar Reservoir - Fort
Loudoun Reservoir - Melton Hill Reservoir Watershed in 1993. One of these sites was a stream
monitoring site at Emory River mile (EmRM) 14.5. Six of the locations (TRMs 530, 560, 570,
600, and 625 and CRM 1) were sampled for continuation of the trend studies on Watts Bar and
Fort Loudoun Reservoirs initiated in the mid to late 1980s. Three locations on Melton Hill
Reservoir were sampled for a special study on embayments near CRM 50. The remaining eight
locations were sampled under contract to DOE for their Clinch River Environmental Restoration
Project (CRERP). The data for the fish collected from the CRERP sites in 1993 were not
available at the time this report was prepared. Historical data from monitoring sites within the
waiersned are available in publications listed in Appendix B.
9.2 Screening Studies
Five channel catfish and largemouth bass were collected from a stream monitoring
location at EmRM 14.5 and analyzed for lipids, pesticides, PCBs, and selected metals from the
EPA Priority Pollutant List. Field handling and processing and laboratory processing were
performed according to the methods for screening studies outlined in Appendix C.
Physical information and the results of metals and organics analyses for this stream
monitoring site are included in Appendix A. Mercury contamination in channel catfish (0.40
-------
|ig/g) and largemouth bass (0.51 (ig/g) were the only analytes which were near or above Tier 2
levels. Several years of fish tissue data exist for this site, so it will not be sampled until summer
1995.
9.3 Trend Studies
9.3.1 Watts Bar Reservoir
Extensive PCB examinations of fish from Watts Bar Reservoir have been conducted for
several years. Earlier collections (1985-88) identified substantial PCB contamination in catfish
and striped bass (Dycus and Hickman 1988; Dycus 1990c). The tailwaters area of Fort Loudoun
Dam was first examined in 1985, and the study reach was expanded downstream each year
thereafter. The first collection of fish from the entire length of Watts Bar Lake was in 1988.
This report describes the results of PCB analyses for the trend study on Watts Bar
Reservoir in the fall of 1993 and compares the results with those from previous years. The latest
Public Health Advisory for Watts Bar Reservoir is included in Appendix D.
Methods — Fish were collected from five locations within Watts Bar Reservoir in 1993,
TRMs 530, 560, 570, and 601 and CRM 1. Ten carp were collected from TRMs 530, 560, and
601 and CRM 1; five analyzed as composites and five stored for future reference. Nine channel
catfish from TRM 560 and ten channel catfish from TRM 601 were analyzed individually. Five
white bass collected from each location except TRM 570 and five smallmouth buffalo from TRMs
530, 570 and 601 were analyzed as composites. All fish samples were analyzed for lipids, PCBs,
and chlordane according to the methods in Appendix C.
Results and Recommendations — Physical information and results of chemical analyses
are presented in Tables 9.3.1-1 to 9.3.1-11 and Figure 9.3.1-1. Lipid content in catfish was
significantly different among years but did not reveal any consistent trend. There was a significant
55
-------
interaction between years and locations for catfish weight. This may be the result of smaller fish
captured at certain locations during 1989 and 1990.
Preliminary tests indicated a need to adjust PCB concentration for lipid content and fish
weight in channel catfish. After adjustment, the two-way co-ANOVA statistics for years and
locations indicated inconsistent relationships between lipid content and PCB concentration
(non-parallel lines). However, since the P value for parallel line test for lipid content was very
near the acceptance level (a=0.05), the results of the co-ANOVA are valid for fish with close to
mean weight and lipid content. The co-ANOVA indicated, except for fish collected in 1992, fish
collected in 1988 had significantly higher PCB concentrations than ones collected in the other
years. Fish with weights and lipid contents near the extremes may show a different pattern.
Visual examination of the results and a one-way ANOVA comparing year differences for
each site indicate lower mean PCB concentrations in catfish from TRM 560 in 1989 and 1990
than in other years. These low mean PCB concentrations coincide with lower mean weight of
fish.
PCB concentrations in white bass (maximum in 1993 of 0.6 ng/g), smallmouth buffalo
(maximum in 1993 of 1.4 ng/g), and carp (maximum in 1993 of 0.7 ng/g) are lower than levels
found in previous years from corresponding sites. Fish tissue studies need to be continued on
Watts Bar Reservoir. Specific plans for autumn 1994 will be developed after coordination with
state agencies and ORNL. At a minimum, channel catfish should be collected at selected
locations to examine the trend in PCB concentrations; possibly one to three 5-fish composites
from TRMs 532, 560, and 600.
56
-------
Table 9.3.1-1 Physical information for channel catfish, carp, white bass, and smallmouth buffalo
collected from Watts Bar Reservoir, 1993.
Collection Site
Collection Date
Species'
Length (mm)
Weight (g)
Sex'
LABID'
TRM 530.2
10
6
93
WHB
362
680
MALE
33056
TRM 530.2
10
6
93
WHB
403
848
FMALE
33056
TRM 530.2
10
6
93
WHB
360
638
FMALE
33056
TRM 530.2
10
6
93
WHB
365
690
FMALE
33056
TRM 530.2
10
6
93
WHB
391
756
FMALE
33056
TRM 530.2
10
6
93
SBU
653
4524
MALE
33054
TRM 530.2
10
6
93
SBU
653
4886
MALE
33054
TRM 530.2
10
6
93
SBU
489
2136
MALE
33054
TRM 530.2
10
6
93
SBU
561
3516
FMALE
33054
TRM 530.2
10
6
93
SBU
595
4230
MALE
33054
TRM 530.2
10
6
93
c
628
3600
FMALE
33033
TRM 530.2
10
6
93
c
583
2998
FMALE
33033
TRM 530.2
10
6
93
c
619
3568
FMALE
33033
TRM 530.2
10
6
93
c
597
2698
MALE
33033
TRM 530.2
10
6
93
c
636
3350
FMALE
33033
TRM 559.6
10
22
93
CHC
629
2590
FMALE
33059
TRM 559.6
10
22
93
CHC
609
1190
MALE
33061
TRM 559.6
10
22
93
CHC
549
1440
FMALE
33064
TRM 559.6
10
22
93
CHC
471
1048
MALE
33066
TRM 559.6
10
22
93
CHC
395
500
FMALE
33069
TRM 559.6
10
22
93
CHC
400
510
FMALE
33070
TRM 559.6
12
3
93
CHC
490
1054
FMALE
33071
TRM 559.6
12
3
93
CHC
475
822
FMALE
33072
TRM 559.6
12
3
93
CHC
428
620
MALE
33075
TRM 559.6
10
22
93
C
722
5272
FMALE
33077
TRM 559.6
10
22
93
C
618
3176
FMALE
33077
TRM 559.6
10
22
93
C
650
4732
FMALE
33077
.TRM 559.6
10
22
93
C
515
1936
1
33077
TRM 559.6
12
2
93
C
602
3118
FMALE
33077
TRM 559.6
10
22
93
WHB
362
642
FMALE
33098
TRM 559.6
10
22
93
WHB
399
902
FMALE
33098
TRM 559.6
10
22
93
WHB
373
750
FMALE
33098
TRM 559.6
10
22
93
WHB
343
616
FMALE
33098
TRM 559.6
10
22
93
WHB
347
560
MALE
33098
TRM 570
10
20
93
SBU
590
3418
FMALE
33101
TRM 570
10
20
93
SBU
656
4456
FMALE
33101
TRM 570
10
20
93
SBU
588
3538
1
33101
TRM 570
10
20
93
SBU
573
3410
I
33101
TRM 570
10
20
93
SBU
517
1056
I
33101
TRM 570
10
20
93
WHB
331
506
MALE
33117
TRM 570
10
20
93
WHB
356
578
FMALE
33117
TRM 570
10
20
93
WHB
357
608
FMALE
33117
TRM 570
10
20
93
WHB
354
558
FMALE
33117
TRM 570
10
20
93
WHB
339
524
MALE
33117
TRM 600
10
8
93
CHC
418
588
DL
33132
TRM 600
10
g
93
CHC
438
848
DL
33133
TRM 600
10
8
93
CHC
390
564
DL
33134
57
-------
Collection Site
Collection Date
Species*
Length (mm)
Weight (g)
Sex'
LABID"
TRM600
10
8
93
CHC
645
2058
DL
33119
TRM600
10
8
93
CHC
626
2884
DL
33122
TRM600
10
8
93
CHC
385
442
DL
33135
TRM 600
10
8
93
CHC
408
462
DL
33153
TRM600
12
9
93
CHC
387
458
MALE
33154
TRM 600
12
9
93
CHC
430
518
MALE
33155
TRM 600
12
9
93
CHC
409
484
MALE
33156
TRM 600
10
8
93
SBU
482
1584
DL
33159
TRM600
10
8
93
SBU
490
2044
DL
33159
TRM 600
10
8
93
SBU
352
628
DL
33159
TRM 600
10
8
93
SBU
322
542
DL
33159
TRM 600
10
8
93
SBU
332
538
DL
33159
TRM 600
10
8
93
c
522
1910
DL
33124
TRM 600
10
8
93
c
557
2004
DL
33124
TRM 600
10
8
93
c
629
3724
DL
33124
TRM 600
10
8
93
c
512
1952
DL
33124
TRM 600
10
8
93
c
488
1482
DL
33124
TRM 600
10
8
93
WHB
334
460
DL
33161
TRM 600
10
8
93
WHB
335
584
DL
33161
TRM 600
10
8
93
WHB
331
458
DL
33161
TRM 600
10
8
93
WHB
313
402
DL
33161
TRM 600
10
8
93
WHB
279
317
DL
33161
CRM 1.0
10
18
93
c
607
2984
DL
33164
CRM 1.0
10
18
93
C
711
5504
DL
33164
CRM 1.0
10
18
93
C
603
3016
DL
33164
CRM 1.0
10
18
93
C
591
2890
DL
33164
CRM 1.0
10
18
93
C
653
3656
DL
33164
CRM 1.0
10
19
93
WHB
378
694
FMALE
33187
CRM 1.0
10
19
93
WHB
366
596
FMALE
33187
CRM 1.0
10
19
93
WHB
356
662
MALE
33187
CRM 1.0
10
19
93
WHB
331
492
MALE
33187
CRM 1.0
10
19
93
WHB
318
468
FMALE
33187
a WHB = white bass, SBU = smallmouth buffalo, C = carp, CHC = channel catfish
b LABID is a tracking number issued by TVA's Environmental Chemistry Lab. It is used to link a sample's physical and chemical data,
c I = immature, DL - Data on sex and internal and external observations for these fish were lost because of an error in a prototype computer
program
58
-------
Table 9.3.1-2 Concentrations of analytes in channel catfish, carp, white bass, and smallmouth
buffalo collected from Watts Bar Reservoir, 1993.
Collection Site
Species'
LAB1D"
% Lipid
PCB
Chlordane
TRM 530.2
TRM 559.6
TRM 600
CRM 1.0
C
C
C
C
33033
33077
33124
33164
3.7
3.6
3.0
3.2
0.4
0.5
0.6
0.7
<0.01
0.01
<0.01
0.05
TRM 559.6
TRM 559.6
TRM 559.6
TRM 559.6
TRM 559.6
TRM 559.6
TRM 559.6
TRM 559.6
TRM 559.6
TRM 600
TRM 600
TRM 600
TRM 600
TRM 600
TRM 600
TRM 600
TRM 600
TRM 600
TRM 600
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
CHC
33059
33061
33064
33066
33069
33070
33071
33072
33075
33132
33133
33134
33119
33122
33135
33153
33154
33155
33156
4.4
1.3
2.0
4.8
3.8
5.3
4.3
2.0
3.3
1.4
4.5
4.9
1.1
8.1
2.1
0.5
0.7
0.6
1.4
2.1
1.1
2.0
1.0
0.4
0.4
2.3
0.5
0.7
0.2
2.0
1.0
0.9
3.6
0.4
<0.1
0.2
1.6
0.6
0.02
0.01
0.04
0.01
<0.01
<0.01
0.05
0.01
0.01
<0.01
0.15
0.04
0.04
0.21
<0.01
<0.01
<0.01
0.4
0.05
TRM 530.2
TRM 570
.TRM 600
SBU
SBU
SBU
33054
33101
33159
8.8
7.3
4 1
1.4
0.7
0.2
0.02
0.02
0.01
TRM 530.2
TRM 559.6
TRM 570
TRM 600
CRM 1.0
WHB
WHB
WHB
WHB
WHB
33056
33098
33117
33161
33187
2.6
3.4
4.6
3.7
3.1
0.3
0.3
0:6
0.1
0.6
<0.01
0.01
<0.01
<0.01
<0.01
a WHB = white bass, SBU = smallmouth buffalo, C = carp, CHC = channel catfish
b LABID is a tracking number issued by TVA's Environmental Chemistry Lab. It is used to link a sample's
physical and chemical data.
59
-------
Table 9.3.1-3 Summary of lengths, total weights, and percent lipids of catfish from the
Tennessee River portion of Watts Bar Reservoir, 1993 and previous years.
TRM 530/532
TRM545
TRM 557-565
TRM 570/573
TRM 598/600
Year
Length
Range
Mean
Length
Weight
Range
Mean
Weight
% Lipid
Range
Mean %
Lipid
1988
398-706
531
494-4210
1763
0.7-16.0
4.6
1989"
342-562
465
320-1695
1033
1.0-5.0
2.9
1990
354-560
423
322-2110
700
0.2-7.1
3.1
1991
464-609
515
899-2323
1342
1.6-11.0
5.3
1992
380-695
500
407-4178
1514
2.4-11.0
5.4
1993b
b
b
b
b
b
b
1991
385-555
451
548-1358
898
1.4-11.4
3.9
1992"
b
b
b
b
b
b
1987
310-561
470
239-1786
1103
1.4-3.8
2.5
1988
390-657
492
411-2765
1124
0.9-13.0
5.5
1989"
347-500
398
324-1015
544
0.8-4.3
2.1
1990
341-544
438
282-1521
838
0.2-6.0
3.2
1991
488-653
557
1149-2812
1571
0.4-20.0
7.2
1992
427-1559
641
497-3563
1540
0.3-15.0
6.9
1993
395-629
494
500-2590
1086
1.3-5.3
3.5
1987
436-640
492
806-2814
1225
1.5-8.3
4.9
1988
346-615
450
264-2425
929
0.2-7.6
3.7
1989
339-649
466
431-2742
1063
1.5-6.4
3.9
1990
427-512
473
627-1557
930
0.2-8.7
3.5
1991
391-603
505
537-1815
1189
1.0-15.0
5.7
1992b
b
b
b
b
b
b
1987
360-523
457
336-1330
757
3.3-7.3
5.3
1988
452-659
504
829-2957
1289
2.1-8.5
5.2
1989
382-666
514
425-3229
1437
0.8-14.0
5.9
1990
325-600
436
208-3246
912
0.7-14.0
3.8
1991
304-584
446
466-1881
967
1.1-11.0
5.1
1992
360-590
476
464-2168
1018
1.0-9.9
4.4
1993
385-645
454
442-2884
931
0.5-8.1
2.5
a. ORNL data
b. Channel catfish collected by TVA for DOE as part of Clinch River Environmental
Restoration, data not available at the time this report was prepared.
60
-------
Table 9.3.1-4 Summary of lengths, total weights, and percent lipids of catfish from the Clinch
River portion of Watts Bar Reservoir, 1993 and previous years.
Length Range Mean Length Weight Range Mean Weight % Lipid Mean %
CRM 0.5/2.0
CRM 9/10
CRM 20/21
1988
435-605
510
745-2262
1278
0.1-11.0
5.3
1989"
368-620
435
393-2380
794
1.0-5.8
3.3
1990
365-529
437
361-1854
846
2.1-8.2
4.9
1991
475-564
516
585-2151
1199
1.5-14.0
6.5
1992"
b
b
b
b
b
b
1993b
b
b
b
b
b
b
1989*
400-523
440
521-1505
755
0.4-6.4
3.5
1990*
371-574
451
402-2152
835
0.1-7.3
1.7
1991*
390-514
436
450-1334
725
0.9-7.2
4.4
1992*
390-528
439
506-1494
767
0.9-5.12
2.7
1993b
b
b
b
b
b
b
1988
370-790
513
406-6118
1774
1.0-11.5
3.8
1989"
374-530
443
414-1321
736
0.3-7.0
3.3
1990*
370-520
429
373-996
588
0.1-3.1
1.3
1991*
405-502
457
465-1003
760
0.1-6.2
2.6
1992*
374-581
447
452-1985
809
0.2-5.1
3.0
EmRM 1 1993
a. ORNL data
b. Channel catfish collected by TVA for DOE as part of Clinch River Environmental
Restoration Project, data not available at the time this report was prepared.
61
-------
Table 9.3.1-5 Two-way analysis of variance (location and year main effects) and Ryan-Einot-
Gabriel-Welsch Multiple Range Test on lipid content and total weight in channel
catfish from Watts Bar Reservoir, 1988-1993.
CHANNEL CATFISH
P>F
REGW Multiple Range Test"
Mean Rank Low to High
Lipid content Location 0.7200
Year 0.0158 1993 1990 1989 1987 1992 1988 1991
Interaction 0.1351
Total Weight
Location
Year
0.8119
0.0448
Interaction 0.0330
Significant Interaction
a Years or locations underscored by the same lines were not significantly different at a = 0.05.
Years and locations not so underscored were significantly different.
62
-------
Table 9.3.1-6 Summary of total PCB concentrations (ng/g) in catfish fillets from Watts Bar
Reservoir, 1987 to 1993.
TRM
530-532
TRM 545
TRM
557-562
TRM
570-573
TRM
598-600
CRM 0.5-2.0
CRM 9.0-9.3
CRM 19-2C
1987
Range
0.1-4.4
0.9-3.0
0.4-3.1
Mean
1.4
2.1
1.5
Number > 2.0ng/g
1
6
3
Number offish
6
10
10
1988
Range
0.1-4.3
1.3-7.5
0.1-7.4
0.8-4.4
0.1-4.6
0.2-2.4
Mean
1.4
2.7
2.1
2.4
2.2
0.6
Number > 2.0(ig/g
4
6
4
5
4
1
Number offish
10
10
10
10
8
8
1989
Range
0.2-1.5'
0.1-0.5"
0.2-2.5
0.4-4.2
0.2-3.8"
0.3-2.1"
0.9-3.1"
Mean
0.8
0.3
1.3
1.8
1.0
0.8
1.2
Number > 2.0jig/g
0
0
3
2
1
1
1
Number offish
10
9
10
7
10
8
8
1990
Range
<0.1-2.7
<0.1-1.8
<0 1-2.2
0.3-5.8
0.2-4.2
0.2-0.8*
0.5-1.1"
Mean
0.6
0.8
0.7
1.6
1.1
0.4
0.8
Number > 2.0ng/g
1
0
1
3
1
0
0
Number of fish
10
10
10
10
10
8
8
1991
Range
0.8-2.9'
0.3-3.6
0.8^.0"
0.7-2.4"
0.5-4.4
1.2-5.2"
0.2-2.2"
0.4-2.4'
Mean
1.6
1.1
2.3
1.4
1.4
2.6
1.1
1.4
Number > 2.0fig/g
3
1
6
2
2
8
1
1
Number offish
10
10
10
10
10
10
8
8
1992
Range
0.3-5.6
0.2-3.8
0.4-6.2
0.36-3.9"
<0.1-1.1"
Mean
1.7
1.9
1.9
1.3
0.4
Number > 2.0(ig/g
3
6
2
2
0
Number offish
10
(20)'
10
(20)'
10
(19)'
8
8
1993
Range
0.4-2.3
0.1-3 6
Mean
1.2
1.1
Number > 2.0(ig/g
3
2
Number offish
(10)'
9
10
(10)'
(10)'
a. ORNLdata
b. number in ( ) is number of fish collected for DOE
c. 20 additional channel catfish were collected from CRM 20 in spring 1993 for DOE, data not available at the time this report was prepared
d These results are part of the Clinch River Environmental Restoration Project conducted by TVA under contract to the United States
Department of Energy. Data should be considered preliminary until validated by DOE.
63
-------
Table 9.3.1-7 Results of preliminary tests to determine if PCBs should be adjusted for weight and
lipid content and Two-Way Analysis of Covariance used to compare location and
year differences in PCB concentrations in channel catfish from Watts Bar
Reservoir, 1987-1993.
Preliminary Test
(Is there a
significant
relationship
Decision based
between analyte
on preliminary
Test for parallel
Parameter
and parameter)
test
lines
Lipid content
Yesa
Adjust for
P>F = 0.0439
(P>F = 0.0001)
lipid8
lines not parallel
Weight
Yes
Adjust for
P>F = 0.1263
(P>F = 0.0002)
weight
lines parallel
Analysis of
covariance results
assuming parallel
linesb
PCB
0.2524
(locations not
significantly different)
0.0231
(significant difference
among years)
a. Since preliminary tests (not shown) indicated adjusting for both lipids and weight, a test was conducted
where lipids and weight were considered together. This test indicated a need to adjust for both
lipid content and weight.
b. Since tests for parallel lines for lipid content was very close to the acceptance level (a=0.05), the analysis
of covariance results hold true for fish with weights and lipid contents near the mean, but not for
fish with weights and lipid contents near the extremes.
c. 1989 1993 1990 1991 1987 1992 1988
Table 9.3.1-8 One-Way Analysis of Variance and Ryan-Einot- Gabriel-Welsch Multiple Range
Test comparing year differences for individual sites in PCB concentrations in
channel catfish from Watts Bar Reservoir, 1993.
REGW Multiple Range Test4
Location P>F Mean Rank Low to High
560 Year 0.0001 1989 1990 1987 1993 1992 1991 1988
600 Year 0.2420 No Significant Difference
a Years or locations underscored by the same lines were not significantly different at a = 0.05.
Years and locations not so underscored were significantly different.
64
-------
Table 9.3.1-9 Summary of lengths, total weights, percent lipids, and PCB concentration in white
bass from Watts Bar Reservoir, 1993 and previous years.
Year
Length
Range
Mean
Length
Weight
Range
Mean
Weight
% Lipid
Range
Mean %
Lipid
PCB
Range
Mean
PCB
TRM530
1993"
360-403
376
638-848
722
a
2.6
a
0.3
TRM560
1993"
343-399
365
560-902
694
a
3.4
a
0.3
TRM 570/573
1987'
344-396
370
606-904
738
a
6.1
a
0.8
1992
329-395
359
483-744
583
0.4-7.8
3.8
A
©
1
0.7
1993*
331-357
343
506-608
555
a
4.6
a
0.6
TRM585
1987'
352-363
357
518-708
644
a
6.1
•
0.9
TRM 601
1993'
279-335
318
317-584
444
3.7
a
0.1
CRM 1
1993*
318-378
350
468-694
582
a
3.1
a
0.6
a White bass analyzed as composites (no ranges for analytes)
65
-------
Table 9.3.1-10 Summary of lengths, total weights, percent lipids, and PCB concentration in carp
from Watts Bar Reservoir, 1993 and previous years.
Length Mean Weight Mean Mean % Mean PCB
Year Range Length Range Weight Lipid
TRM530 1993" 583-636 613 2698-360 3243 3.7 0.4
TRM560 1993a 515-722 621 1936-527 3647 3.6 0.5
TRM 598/601 1987° 469-583 543 1575-256 2238 1.6 2.7
1993s 488-629 542 1482-372 2214 3.0 0.6
CRM.l 1993s 591-711 633 2890-550 3610 3.2 0.7
a Carp analyzed as composites (no ranges for analytes)
66
-------
Table 9.3.1-11 Summary of lengths, total weights, percent lipids, and PCB concentration in
smallmouth buffalo from Watts Bar Reservoir, 1993 and previous years.
Length Mean Weight Mean % Lipid Mean % PCB Mean
Year Range Length Range Weight Range Lipid Range PCB
TRM532
1988"
580
b
3280
b
12.0
b
0.4
b
1993*
489-653
590
2136-4886
3858
a
8.8
•
1.4
TRM 570/573
1987'
436-608
526
1276-4261
2619
a
8.4
a
3.1
1988
480-537
505
1750-2933
2289
9.2-20.0
14.6
0.2-1.4
0.8
1993*
517-656
585
1056-4456
3176
•
7.3
a
0.7
TRM601
1993*
322-490
396
538-2044
1067
a
4.1
a
0.2
a Smallmouth Buffalo analyzed as composites (no ranges for analytes)
b Only one smallmouth buffalo collected (no means)
67
-------
Figure 9.3.1-1 Mean PCB concentrations (jig/g) in catfish from individual sites, TRM 530-532, TRM 557-562, TRM 570-573 and TRM
598-600, on Watts Bar Reservoir, 1987-1993.
TRM 530-532
1987
1988
1989
1990
1991
1992
1993
3
2.5
2
1 5
1
0.5
0
TRM 557-562
1987
1988 1989 1990 1991
1992 1993
TRM 570-573
TRM 598-600
1987
1988 1989 1990 1991
1992
1993
3
2.5
2
1.5
1
0.5
0
1987
1988 1989 1990 1991
1992 1993
-------
9.3.2 Fort Loudoun Reservoir
Contamination of catfish (mostly channel catfish) and largemouth bass with PCBs in Fort
Loudoun Reservoir, especially the Little River embayment, has been known for several years.
Several warnings and advisories (the latest is Appendix D) have been issued by TDEC against
consumption of catfish and certain largemouth bass from Fort Loudoun Lake. Tennessee Wildlife
Resources Agency (TWRA) has banned commercial fishing for catfish from this reservoir.
Intensive sampling of channel catfish has continued at TRM 624-628 to examine
long-term trends. Although significant differences among years have been found, no consistent
temporal pattern has been perceptible through 1992 (Williams and Dycus, 1993). PCB
concentrations in white bass (0.5 ng/g) and carp (0.6 ng/g) collected from TRM 651 in 1992
were relatively low.
This document describes the results of PCB analyses of catfish from TRM 624 collected in
autumn 1993 and compares them to results from previous years. Sample site was moved from
TRM 628 to TRM 624 to obtain "free" fish from other sampling activities.
Methods — Ten channel catfish were collected from TRM 624 in 1993 and analyzed
individually for lipids, PCBs, and chlordane. Field handling and processing and laboratory
processing were performed according to the methods outlined in Appendix C and will not be
repeated here.
Results and Recommendations ~ Physical information and the results of analyses on
channel catfish collected from TRMs 624-629 are contained in tables 9.3.2-1 through 9.3.2-5.
Weights and lipid content of catfish collected in 1993 were not significantly different from
previous years. Results of a co-ANOVA on PCB concentrations adjusted for weight indicated
concentrations in 1993 were significantly lower than concentrations in 1989, 1991, and 1992 but
69
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were not significantly different from other years. No overall trend in PCB concentrations in
channel catfish from this site can be determined.
Channel catfish from this site should continue to be analyzed to keep abreast of the
situation and provide data for fish consumption advisories issued by TDEC.
Table 9.3.2-1 Physical data and analyte concentrations (|ig/g) in channel catfish collected from
TRM 624, Fort Loudoun Reservoir, on November 12, 1993.
LABID"
Sex
Length
Weight
% Lipids
PCB
Chlordane
33198
FMALE
526
1286
0.9
1.3
0.07
33200
FMALE
569
1950
2.4
1.1
0.02
33203
FMALE
586
1824
2.5
1.7
0.02
33205
FMALE
542
1466
5.4
2.2
0.02
33208
FMALE
515
1110
3.4
1.3
0.04
33210
FMALE
491
978
5.2
2.0
0.04
33213
MALE
516
1276
6.4
0.8
0.01
33214
MALE
408
490
1.1
0.5
<0.01
33215
MALE
407
566
1.2
0.7
<0.01
33216
MALE
381
432
2.7
0.4
<0.01
a LABID is a tracking number issued by TVA's Environmental Chemistry Lab. It is used to link a sample's
physical and chemical data.
70
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tie 9.3.
Catfisl
1985
1987
1988
1989
1990
1991
1992
1993
Carp
1992
rhite B
1987"
1992
Summary of lengths, total weights, and % lipids of catfish, carp, and white bass from Fort Loudoun Reservoir,
collected from 1985 to 1993.
Location
TRM Weight Range Mean Weight Length Range Mean Length % Lipid Range Mean % Lipid
628 270-2720 834 330-655 441 2.8-5.6 3.9
628 580-2275 1385 410-645 507 0.2-11.0 4.5
628 538-1732 968 391-577 465 0.8-11.0 5.4
628 292-2169 1002 344-573 474 0.6-14.0 4.4
628 375-1720 866 375-545 458 0.3-5.0 2.5
624 461-2139 1049 401-605 489 0.8-5.6 3.3
624 430-1291 679 368-520 432 0.5-6.1 2.7
624 432-1950 1138 381-586 494 0.9-6.4 3.1
651 1219-1937 1594 438-520 489 3.2-12.0 6.9
628 162-180 181 221-239 233 a 3.1
640 275-606 435 259-330 302 a 5.8
651 460-633 534 318-356 337 3.6-5.6 4.6
a. Five white bass were collected from TRMs 628 and 640 in 1987. Each set of five was analyzed as a composite sample.
73
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Table 9.3.2-3 Results of one-way ANOVA and REGW Multiple Range Test examining
differences among years in lipid content and total weight in catfish from
TRM 624-629, Fort Loudoun Reservoir.
CATFISH
REGW Multiple Range Test3
P>F Mean Rank Low to High
Lipid content Year 0.2397 No Significant Difference
Total Weight Year 0.0236 1985 1992 1990 1989 1991 1988 1993 1987
a. Years underscored by the same lines were not significantly different at a = 0.05.
74
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Table 9.3.2-4 Summary of PCB concentrations in catfish, carp, and white bass from Fort
Loudoun Reservoir, collected from 1985 to 1993.
Location PCB Range
TRM
Catfish
1985 628 0.2-2.8
1987 628 0.1-4.5
1988 628 0.2-4.4
1989 628 0.6-4.3
1990 628 0.3-1.9
1991 624 1.4-4.6
1992 624 0.1-4.2
1993 624 0.4-2.2
Carp
1992 651 0.2-0.9
White Bass
1987" 628 b
640 b
1992 651 0.3-1.2
Mean Number > 2.0 Number offish
Hg/g
1.4 2 10
1.5 2 10
1.2 1 10
2.3 11 10
1.0 0 10
2.5 7 10
1.8 3 9
1.2 2 10
0.6 0 10
<0.1 a 5
<0.1 a 5
0.5 0 10
a. Catfish were sampled from TRMs 624-629. White bass and carp were collected from TRM 651 in 1992.
b. Five white bass were collected from TRMs 628 and 640 in 1987. Each set of five was analyzed as a composite
sample.
75
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Table 9.3.2-5 Results of statistical tests used to compare yearly differences in PCB
concentrations in catfish from TRMs 624-629, Fort Loudoun Reservoir,
1985-1993.
Analyte
Parameter
Preliminary Test
(Is there a
significant
relationship
between analyte
and parameter)
Decision based
on preliminary
test
Test of parallel Analysis of
lines covariance results
PCB
Lipid content
Weight
No
(P>F = 0.1632)
Yes
(P>F = 0.0128)
Do not adjust
for lipid
Adjust for
weight
P>F = 0.8877
lines parallel
P>F = 0.0001
Years are different
Years underscored by the same lines were not significantly different at a = 0.05.
1990 1988 1993 1987 1985 1992 1989 1991
76
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Figure 9.3.2-1 Mean PCB concentrations (|!g/g) in catfish from TRM 624 on Fort Loudoun
Reservoir, 1985-1993.
-j
oi2.5
D)
CO
1.5
0
o
c
o
O
CQ
cl 0.5
1
0
1985 1986 1987 1988 1989 1990 1991 1992 1993
Year
-------
9.4 Special Study — Three Embavments on Melton Hill Reservoir
Melton Hill Reservoir is currently in the trend study stage. A potential PCB problem (in
catfish only) was first documented in 1984. Two of 22 catfish collected from Melton Hill
reservoir had detectable PCB concentrations (one in McCoy Branch, 1.0 ng/g; one at Melton Hill
Dam, 4.7 ng/g) (TVA 1985). Since the latter was collected at the face of the dam, it could have
been transported from below the dam during navigation lock operations.
Results from the Valley-wide Fish Tissue Screening Study in 1987 found concentrations of
PCBs and chlordane sufficiently high to warrant more in-depth study (Dycus 1989a). The
five-fish composites from lower and mid-reservoir areas (CRMs 23 and 39) contained 1.2 and
2.0 ng/g PCBs and 0.16 ng/g chlordane each.
Subsequent studies in 1988 and 1989 lead to the TDEC issuing an advisory against
consumption of catfish from Melton Hill Reservoir in April 1989 (Dycus 1990c). The most recent
advisory is included in Appendix D.
The study was continued in 1990 - two of ten channel catfish (mean of 1.2 |ig/g) collected
by TVA at CRM 51 had PCB concentrations above 2.0 ng/g. The mean PCB concentration of
channel catfish at CRM 23, collected and analyzed by ORNL, was 0.5 |ig/g (after adjustment
(actual PCB value multiplied by 1.5) to account for low spike recoveries in Q/A samples).
In 1991 and 1992 channel catfish were collected and analyzed from CRMs 24, 39, and 51
by TVA and ORNL. PCB concentrations were generally higher in 1991 than in previous years,
with concentrations in 1992 generally similar to previous years. There were no statistically
significant differences among years or sites.
This section describes the results of PCB analyses of catfish collected from three
embayments near CRM 51 on Melton Hill Reservoir in the autumn of 1993 by TVA. Historically
one or two catfish collected each year at the CRM 51 had high levels of PCBs. This could
78
-------
suggest that some of the fish move into and out of areas of locally high PCB concentrations. To
further examine this possibility, Tennessee DOE Oversight Division identified three embayments
(Figure 9.4-1) near the CRM 51 monitoring site which might be potential sources ofPCBs. TVA
collected and analyzed channel catfish from two of the embayments (CRMs 51.1 and 50.1) and
carp (no catfish could be collected) from the other (CRM 49.5) for PCBs, chlordane, and lipids.
Methods — In 1993, five channel catfish were collected from embayments at CRMs 51.1
(embayment #1) and 50.1 (embayment #2) and five carp (catfish were not available) were
collected from the embayment at CRM 49.5 (embayment #3). These fish were analyzed as
composites for PCBs, chlordane and lipids. Procedures involved in field sampling and processing,
laboratory and data analyses were similar to those described Appendix C, except fish baskets were
used to collect catfish at embayment #1 because of inaccessibility of the embayment.
Results and Recommendations -- Results of the 1993 study are in Table 9.4-1. PCB
concentrations in channel catfish from embayments #1 (0.7 |ig/g) and #2 (0.9 jig/g) were similar
to one another. PCB concentration in carp (embayment #3) was only 0.1 ng/g. Although a more
in-depth study would be necessary to rule out these embayments as potential contributors of high
PCB concentrations in fish collected in previous years, results of this special study do not support
the need for a more in-depth investigation. Ten channel catfish should be collected from CRM 51
in autumn 1994 to determine how concentrations compare to previous years. ORNL will examine
catfish from CRM 23 in 1994.
79
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Table 9.4.1-1 Physical information, lipid content, PCB, and chlordane concentrations of channel
catfish and carp composites collected for the three embayment study on Melton
Hill Reservoir, 1993.
Embayment #1 CRM 51.2
Channel Catfish #1
Channel Catfish #2
Channel Catfish #3
Channel Catfish #4
Channel Catfish #5
Composite
LABID Weight Length Lipid Chlordane PCB
33190
1132
1064
626
566
506
490
462
432
428
391
5.3
0.02
0.7
Embayment #2 CRM 50.1
Channel Catfish #1
Channel Catfish #2
Channel Catfish #3
Channel Catfish #4
Channel Catfish #5
Composite
1328
964
1004
1038
886
547
458
482
472
478
33192
5.2
0.06
0.9
Embayment #3 CRM 49.5
Carp #1
Carp #2
Carp #3
Carp #4
Carp #5
Composite
1678
1866
2086
1046
694
523
537
549
425
367
33195
1.1
<0.01
0.1
80
-------
8001
84°12'30" 2.530 o;g feet
"7 virvi—;—
CLINTON 3 4 Ml y
^ ; ^r
% Figure 9.4-1 Locations of the three embayments sampled in
1993 from Melton Hill Reservoir
(See Chart
ID ¦
CO
O
o
CO
WARNING
This navigation chart has not been updated for several years
and ma/ not reflect changes that may have occurred in loca-
tions oi navigation aids, underwater installations, hazards,
obstructions, bridges, aerial electrical crossings, and other
structures since the last revision of the chart. Navigators and
. others who use th,s chart da so at their own risk, and TV A
assumes no liability or responsibility whatsoever lor reservoir
features, and structures that are not shown or that may be
incorrectly shown on this chart.
_L
84°12'30'
2.540.000 FEET
(See Chart 1002j
The Tennessee V.illey Authority plans to moke periodic revisions and additions to the navigation aids on this chart, but Deco
on the river for latest revisions see published Coast Guard Light List* Copies of this series of charts may oe purchased
-------
Chapter 10
Clinch River-Powell River Watershed
wv s
~
A
o
+
Stream Monitoring Sites sampled in 1993
Stream Monitoring Sites not sampled in 1993
Reservoir Monitoring Sites sampled in 1993
Reservoir Monitoring Sites not sampled in 1993
DOE Clinch River Environmental Restoration Project
CRM 80
Mercury concentrations In largemouth bass (0.S9 fig/g)
sufficiently high to warrant further Investigation.
00
to
Watts Bar Reservoir-Fort Loudoun Reservoir-
Melton Hill Reservoir Watershed
-------
Chapter 10.0 Clinch River - Powell River Watershed
10.1 Introduction
Fish tissue samples were collected from five sites in the Clinch River - Powell River
Watershed in 1993. Two of the locations were stream monitoring sites, one on the Powell River
(PRM 65) and one on the Clinch River (CRM 172). Three locations were reservoir monitoring
sites in Norris Reservoir, CRMs 80 and 125 and PRM 30. CRM 125 also served as a reference
site for the DOE Clinch River Environmental Restoration Project. Results of the 1993 DOE
samples were not complete at the time this report was written. Historical data from monitoring
sites within the Clinch River - Powell River Watershed are available in publications listed in
Appendix B.
10.2 Methods
Five channel catfish and five smallmouth bass were collected from the two stream
monitoring sites. Five channel catfish and five largemouth bass were collected from each of the
three reservoir monitoring sites on Norris Reservoir. The smallmouth bass and channel catfish
were analyzed as composites for lipids, pesticides, PCBs, and selected metals on the EPA Priority
Pollutant List. The largemouth bass were analyzed as composites for mercury only. In addition
to composite analysis, each largemouth bass that weighed more than 1200 grams was analyzed
individually for mercury; results for these analyses are included in Appendix F. Field handling and
83
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processing and laboratory processing were performed according to the methods for screening
studies outlined in Appendix C.
10.3 Results and Recommendation
Physical information and the results of metals and organics analyses for the stream and
reservoir monitoring sites are included in Appendix A. Mercury concentration (0.59 ng/g) in
largemouth bass composite (maximum of 0.83 ng/g in one large individual, Appendix F) from the
forebay region of Norris Reservoir was the only contaminant to indicate a need for further
investigation. Reservoir sampling of largemouth bass should be repeated in autumn 1994 to more
thoroughly examine a possible concern for mercury levels. The two stream monitoring sites
should be placed on a two-year rotation and sampled again in 1995.
84
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Watts Bar Reservoir-
Fort Loudoun Reservoir-
Melton Hill Reservoir Watershed
Chapter 11 - Lit
LTRM 1.0
Mercury (0.J6) and PCB (1.4) contamination in channel
catfish warrant continued sampling in 1994.
ZK
LTRM 15
PCBs in channel catfish (1.0 |ig/g) warrant continued
sampling in 1994.
oo
<
/
/
Hiwassee River Watershed
NC
A Stream Monitoring Sites sampled in 1993
A Stream Monitoring Sites not sampled in 1993
• Reservoir Monitoring Sites sampled in 1993
O Reservoir Monitoring Sites not sampled in 1993
Tennessee
River Wate* ^ied
French Broad River Watershed
-------
Chapter 11.0 Little Tennessee River Watershed
11.1 Introduction
A fish consumption advisory is in effect for catfish for all of Tellico Reservoir. Catfish
should not be eaten because of PCB contamination. The most current fish consumption advisory
from TDEC is Appendix D.
Fish tissue samples were collected from six locations in the Little Tennessee River
Watershed in 1993. One was a stream monitoring site at LTRM 94.3. The other five were
reservoir monitoring sites; two in Tellico Reservoir (LTRMs 1 and 15) and three in Fontana
Reservoir (LTRMs 62 and 81 and Tuckasegee River mile (TucRM) 3). The locations in Tellico
Reservoir were sampled as an ongoing trend study of PCB concentrations. The locations in
Fontana Reservoir were sampled to further examine relatively high PCBs and mercury
concentrations observed in autumn 1992. Historical data from monitoring sites within the Little
Tennessee River Watershed are available in publications listed in Appendix B.
11.2 Methods
Five channel catfish and five smallmouth bass were collected from the stream monitoring
site at LTRM 94.3. Five channel catfish were collected from LTRMs 1, 15, and 81 and TucRM
3. Four channel catfish were collected from LTRM 62. These fish were analyzed as composites
for lipids, pesticides, PCBs, and selected metals on the EPA Priority Pollutant List following the
methods outlined in Appendix C.
86
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Five largemouth bass were collected from each of the reservoir monitoring sites and
analyzed as composites for mercury only. In addition to composite analysis, each largemouth bass
that weighed more than 1200 grams was analyzed individually for mercury; results for these
individual analyses are included in Appendix F. Field handling and processing and laboratory
processing were performed according to the methods for screening studies outlined in Appendix
C.
11.3 Results and Recommendations
Physical information and the results of metals and organics analyses for the stream and
reservoir monitoring sites are included in Appendix A. Results for Tellico Reservoir indicate that
PCB levels in channel catfish from the forebay (1.4 jag/g) and mid-reservoir (1.0 |ig/g) locations
continue to remain relatively high. Mercury concentrations (0.56 |ig/g) in catfish from the
forebay of Tellico were sufficiently high to be of interest and possibly warrant further
investigation in autumn 1994. Sampling on Tellico Reservoir should be repeated in autumn 1994.
Results from Fontana Reservoir in 1993 differed substantially from those in 1992, in that PCB
concentrations were much reduced (maximum of 0.4 jxg/g in autumn 1993 compared to 1.4 jig/g
in 1992). Mercury concentrations were also somewhat lower in 1993. Further screening of
Fontana Reservoir should be conducted in 1994 to help determine which data set (1992 or 1993)
is most representative of conditions in Fontana Reservoir. The stream monitoring location at
LTRM 94.3 will be resampled in summer 1994 because this is a relatively new sample site.
Additional mercury results for analyses of largemouth bass from both these reservoirs is in
Appendix F. Interestingly, mercury concentrations in largemouth bass from Tellico Reservoir
87
-------
were lower than in channel catfish, contrary to what would normally be expected. One large
largemouth bass (2774 grams) from Fontana Reservoir contained a high concentration of mercury
(0.94 |ig/g).
88
-------
Ch ter 12 - French Broad ^
A Stream Monitoring Sites sampled in 1993
A Stream Monitoring Sites not sampled in 1993
• Reservoir Monitoring Sites sampled in 1993
O Reservoir Monitoring Sites not sampled in 1993
Holston Watershed
Watts Bar-
Fort Loudoun
Watershed
FBRM 78
Mercury levels in smallmouth bass composite (0.51 ng'g)
were sufficiently high to warrant resampling in summer 1994.
Little Tennessee Watershed
tershed
Holston Watershed
/
SC
-------
Chapter 12.0 French Broad Watershed
12.1 Introduction
Tennessee and North Carolina have issued fish consumption advisories for fish from the
Pigeon River because of dioxin contamination. The most current Tennessee fish consumption
advisory is Appendix D.
Fish tissue samples were collected only from two stream monitoring locations in 1993,
Nolichucky River mile (NRM) 8.5 and French Broad River mile (FBRM) 78. Historical data from
monitoring sites within the French Broad Watershed are available in publications listed in
Appendix B.
12.2 Methods
Five carp and four spotted bass were collected from NRM 8.5 and five channel catfish,
two largemouth bass, and two smallmouth bass were collected from FBRM 78. These fish were
analyzed for lipids, pesticides, PCBs, and selected metals on the EPA Priority Pollutant List.
Field handling and processing and laboratory processing were performed according to the
methods for screening studies outlined in Appendix C.
12.3 Results and Recommendations
Physical information and the results of metals and organics analyses for the stream sites
are included in Appendix A. All analytes, except mercury, had low or nondetectable
90
-------
concentrations. Relatively high concentrations of mercury were found in smallmouth bass (0.51
|ig/g) but not in largemouth bass (0.19 |ig/g) from FBRM 78. The stream monitoring sites at
FBRM 78 and NRM 8.5 will be sampled in summer 1994.
91
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Chapter 13
Holston Watershed
~ Stream Monitoring Sites sampled in 1993
A Stream Monitoring Sites not sampled in 1993
• Reservoir Monitoring Sites sampled in 1993
O Reservoir Monitoring Sites not sampled in 1993
•ff Cove Spring Branch Embayment special study
Cove Soring Branch
Lead and mercury levels in channel catfish and largemouth bass
were consistent with levels in fish from other reservoirs. One
largemouth bass weighing 2580 g. contained a very high
concentration of mercury (1.0 (ig/g).
VA
Clinch-Powell Watershed
VO
to
HRMs S3 and 91
Chlordane levels in channel catfish (0.13 and 0.11 pg'g)
were sufficiently high to warrant resampling 1994.
T.
TN
French Broad Watershed
/
Boone Reservoir
Relatively low concentrations of PCBs and chlordane are
noteworthy and warrant resampling in 1994.
-------
Chapter 13.0 Holston River Watershed
13.1 Introduction
TDEC as issued a precautionary advisory to limit consumption of catfish and carp from
Boone Reservoir because of PCB and chlordane contamination and an advisory against
consuming any fish from the Tennessee portion of the North Fork Holston River because of
mercury contamination. The most current fish advisory is Appendix D.
Fish tissue samples were collected from one stream monitoring site (HRM 109.9) and nine
reservoir monitoring sites in the Holston River Watershed in 1993. Three of the reservoir
monitoring sites were in Cherokee Reservoir (HRMs 53, 75, and 91) and three were in Boone
Reservoir (South Fork Holston River miles (SFHRM) 19 and 27 and Watauga River mile (WRM)
8). Of the remaining three reservoir sites, one was in Fort Patrick Henry Reservoir (SFHRM 9),
one was in Watauga Reservoir (WRM 37), and the other was in South Holston Reservoir
(SFHRM 51). Historical data from monitoring sites within the Holston River Watershed are
available in publications listed in Appendix B.
A special study was conducted in Cove Spring Branch on South Holston Reservoir in
1994. Ten channel catfish and 11 largemouth bass were collected from this site.
13.2 Screening Study
13.2.1 Methods
Five channel catfish and five largemouth bass were collected from each of the ten
monitoring sites. The largemouth bass from HRM 109.9 and the channel catfish from all the sites
93
-------
were analyzed as composites for lipids, pesticides, PCBs, and selected metals on the EPA Priority
Pollutant List. The largemouth bass from the reservoir monitoring sites were analyzed as
composites for mercury only. Largemouth bass weighing over 1360 grams (3 lb.) were analyzed
individually and reported in Appendix F. Field handling and processing and laboratory processing
were performed according to the methods outlined in Appendix C.
13.2.2 Results and Recommendations
Physical information and the results of metals and organics analyses for the stream and
reservoir monitoring sites are included in Appendix A. Chlordane in channel catfish from
Cherokee Reservoir (HRMs 53 and 91) was the only contaminant sufficiently high to be of
interest.
Channel catfish from Cherokee Reservoir should be resampled in autumn 1994 to better
examine chlordane concentrations. The stream monitoring location will be placed on two-year
rotation cycle and be sampled in 1995.
Relatively low or nondetectable concentrations of PCBs and chlordane in channel catfish
samples from Boone Reservoir are noteworthy and could have implications for the precautionary
advisory there. Additional samples from Boone Reservoir should be examined in autumn 1994 to
document if these relatively low concentrations continue to exist.
13.3 Cove Spring Branch Study
Late in 1993, interest was drawn toward an old battery casing dump site on South Holston
Reservoir. This dump is located in Cove Spring Branch embayment and there was concern over
94
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potential mercury and lead contamination. Therefore, a special study was initiated by TV A, the
State of Tennessee, and U.S. Forest Service.
The TVA Holston River Action Team funded a special fish tissue investigation within
Cove Spring Branch embayment. Two composites of five channel catfish, two composites of five
largemouth bass, and one large individual largemouth bass were analyzed for lead and mercury.
Also five fish from the composite samples (one channel catfish and four largemouth bass)
weighing more than 1400 grams were analyzed individually for mercury content. Field handling
and processing and laboratory processing were similar to the methods outlined in Appendix C.
Results of the special study on Cove Spring Branch embayment are in Table 12.3-1. Fish
from Cove Spring Branch did not contain elevated levels of lead. Lead concentrations were either
below or slightly above the laboratory detection limit.
Mercury concentrations in fish composites from Cove Spring Branch were similar to those
in other area reservoirs, indicating no impact from the battery dump. All except one of the large
largemouth bass contained mercury levels near or above the levels suggesting need for further
screening studies.
As might be expected due to its size and age, one largemouth bass weighing over 2580
grams contained a very high concentration of mercury (1 ng/g). Similarly high mercury
concentrations were found in large largemouth bass from several other reservoirs in autumn 1993
as reported in Appendix F. This issue needs to be further examined by additional sampling in
autumn 1994. Specifics for further study had not been developed at the time this report was
prepared.
95
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Table 13.3-1 Results of the special study conducted on lead and mercury concentrations in
channel catfish and largemouth bass from Cove Spring Branch Embayment, South
Holston Reservoir, 1993.
Composites Individuals
Fish Weight Hg Pb Hg
Channel Catfish
#1 976
#2 1,414 0.58
#3 890
#4 754
#5 842
Composite 0.42 <0.02
#9 1,110
#10 906
#11 828
#12 876
#13 684
Composite q.36 0.05
Largemouth Bass
#1 1,402 0.51
#2 1,492 0.43
#3 1,118
#4 1,264
#5 948
Composite 0.41 <0.02
#6 890
#7 1,908 0.63
#8 1,154
#9 1,452 0.24
#10 790
Composite 0.36 0.04
#12 2,580 1.0
96
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REFERENCES
Bates, J. A., D. L. Dycus, and G. E. Hall. 1992. "Reservoir Monitoring - 1991 - Fish Tissue
Studies in the Tennessee Valley in 1990." TVA, River Basin Operations, Water
Resources, Chattanooga, Tennessee. TVA/WR--92/7
Dycus, Donald L. 1986. "North Alabama Water Quality Assessment: Volume VII -
Contaminants in Biota." TVA, Office of Natural Resources and Economic Development,
Air and Water Resources, Knoxville, Tennessee. TVA/ONRED/AWR-86/33.
Dycus, Donald L. 1988. "Levels of Selected Metals and PCBs in Channel Catfish from
Chickamauga Reservoir, 1987." TVA, River Basin Operations, Water Resources.
Dycus, Donald L. 1989a. "Results of Fish Tissue Screening Studies from Sites on the Tennessee
and Cumberland Rivers in 1987." TVA River Basin Operations, Water Resources.
Chattanooga, Tennessee. TVA/WR/AB--89/5.
Dycus, Donald L. 1989b. "PCB Studies on Fish From Watts Bar, Ft. Loudoun, Tellico and
Chilhowee Reservoirs, 1987." TVA, River Basin Operations, Water Resources,
Chattanooga, Tennessee. TVA/AWR-89/10.
Dycus, Donald L. 1990a. "Results of PCB and Chlordane Analyses on Fish Collected from
Nickajack Reservoir in Jan-Feb 1989." TVA, River Basin Operations, Water Resources,
Chattanooga, Tennessee. TVA/WR/AB-90/9.
Dycus, Donald L. 1990b. "Levels of Selected Metals and PCBs in Channel Catfish from
Chickamauga Reservoir, 1988." TVA, River Basin Operations, Water Resources.
Chattanooga, Tennessee. TVAAVR/AB—90/3.
Dycus, Donald L. 1990c. "PCB Studies on Fish from Watts Bar, Fort Loudoun, Tellico, and
Melton Hill Reservoir—1988." TVA River Basin Operations, Water Resources.
Chattanooga, Tennessee. TVA/WR/AB—90/11.
Dycus, D. L., J. P. Fehring and G. D. Hickman. 1987. "PCB Concentrations in Fish and
Sediment from Fort Loudoun Reservoir—1985." Tennessee Valley Authority, Office of
Natural Resources and Economic Development, Knoxville, Tennessee.
TV A/ONRED/AWR-8 8/8.
Dycus, D. L. and G. D. Hickman. 1988. "PCB Levels in Fish from Fort Loudoun Reservoir, Fort
Loudoun Dam Tailrace, Tellico Reservoir, and Chilhowee Reservoir, Autumn 1986 to
Winter 1987." Tennessee Valley Authority, Water Resources, Knoxville, Tennessee.
TVA/ONRED/AWR-88/19.
97
-------
Dycus, D. L. and D. R. Lowery. 1986. "PCB Concentrations in Wilson Reservoir Catfish -
1985." Tennessee Valley Authority, Office ofNatural Resources and Economic
Development, Knoxville, Tennessee. TVA/ONRED/AWR-86/57.
Dycus, D. L. and D. R. Lowery. 1987. "PCB Concentrations in Wilson Reservoir Catfish -
1986." Tennessee Valley Authority, Office ofNatural Resources and Economic
Development, Knoxville, Tennessee. TVA/ONRED/AWR-88/2.
Dycus, D. L. and D. R. Lowery. 1988. "PCB Concentrations in Wilson Reservoir Catfish -
1987." Tennessee Valley Authority, Water Resources, Knoxville, Tennessee.
FWGPM. 1974. "Guidelines on Sampling and Statistical Methodologies for Ambient Pesticide
Monitoring." Federal Working Group on Pesticide Management. Washington, D.C.
October 1974.
Food and Drug Administration. 1987. "Action Levels for Poisonous or Deleterious Substances
in Human Food and Animal Substances." Industrial Programs Branch, Bureau of Foods.
(HFF-336) 200 C St. SW. Washington, D.C.
Gall, K. and Voiland, M. 1990. "Contaminants in Sport Fish: Managing Risks." See Grant
Extension Fact Sheet. Cornell Cooperative Extension. Cornell University, Ithaca, New
York.
Hall, G. E., and D. L. Dycus. 1991. "Fish Tissue Studies in the Tennessee Valley in 1989."
TV A, River Basin Operations, Water Resources, Chattanooga, Tennessee.
TVA/WR/AB—91/12.
Loar, J. M. 1991. "Fifth Annual Report on the ORNL Biological Monitoring and Abatement
Program." Oak Ridge National Laboratory, Oak Ridge, Tennessee.
Loar, J. M. 1992. "Sixth Annual Report on the ORNL Biological Monitoring and Abatement
Program." Oak Ridge National Laboratory, Oak Ridge, Tennessee. ORNL/TN - 12083.
McCracken, W. E. 1983. "Edible Tissue Sampling for Fish Contaminant Analyses" in PCB's.
Human and Environmental Hazards. F. M. D'tri and M. A. Kamurin, Editors. Butterworth
Publishers, Toronto, Canada.
Olin Corporation. 1994. "Huntsville DDT Remedial Action - Huntsville Spring Branch, Indian
Creek Long-Term Monitoring Program Annual Report No. 6." Environmental Affairs
Department, Charleston, Tennessee.
Travis, C. C., F. O. Hoffman, B. G. Baylock, K. L. Daniels, C. S. Gist and C. W. Weber. 1986.
"Preliminary Review of TV A Fish Sampling and Analysis Report." Task Group Five
Report, TVA 86/15, December 1986, pp. 901129.
98
-------
TV A, 1985. "Instream Contaminant Study - Task 4 - Fish Sampling and Analysis."
ONRED/TV A/April 1985.
Williams, D. L. and D. L. Dycus. 1993. "Reservoir Monitoring - 1992 - Fish Tissue Studies in the
Tennessee Valley in 1991 and 1992." TVA, Water Management, Clean Water Initiative,
Chattanooga, Tennessee.
99
-------
APPENDIX A
RESULTS OF THE
1993 FISH TISSUE
SCREENING STUDIES
IN THE TENNESSEE VALLEY
101
-------
Table A-l Specific physical information on individual fish collected for tissue analysis from
stream and reservoir locations as part of screening studies, 1993.
Collection Site Date Species' Length (mm) Weight (g) Sex LABIDb
Duck River
DRM 22.5
6
10
93
CHC
430
704
C
32548
DRM 22.5
6
10
93
CHC
458
834
c
32548
DRM 22.5
6
10
93
CHC
361
370
c
32548
DRM 22.5
6
10
93
CHC
338
313
c
32548
DRM 22.5
6
10
93
CHC
305
226
c
32548
DRM 22.5
6
10
93
SPB
205
107
c
32550
DRM 22.5
6
10
93
SPB
222
125
c
32550
DRM 22.5
6
10
93
SPB
255
196
c
32550
DRM 22.5
6
10
93
SPB
305
362
c
32550
Bear Creek Reservoir
BCM75
11 3
93
CHC
593
2020
FMALE
33238
BCM75
11 3
93
CHC
532
1350
MALE
33238
BCM75
11 3
93
CHC
522
1525
FMALE
33238
BCM75
11 3
93
CHC
476
980
FMALE
33238
BCM75
11 3
93
CHC
440
720
FMALE
33238
BCM75
11 3
93
LMB
522
2265
FMALE
33444
BCM75
11 3
93
LMB
475
1480
MALE
33295
BCM75
11 3
93
LMB
409
990
FMALE
33295
BCM75
11 3
93
LMB
401
925
FMALE
33295
Little Bear Creek Reservoir
LBCRM 12
11 2
93
LMB
356
585
FMALE
33296
LBCRM 12
11 2
93
LMB
377
720
MALE
33296
LBCRM 12
11 2
93
LMB
382
810
FMALE
33296
LBCRM 12
11 2
93
LMB
562
2085
FMALE
33442
LBCRM 12
11 2
93
LMB
406
980
MALE
33296
LBCRM 12
11 2
93
CHC
468
865
MALE
33239
LBCRM 12
11 2
93
CHC
430
710
FMALE
33239
LBCRM 12
11 2
93
CHC
470
855
MALE
33239
LBCRM 12
11 2
93
CHC
536
1510
FMALE
33239
LBCRM 12
11 2
93
CHC
631
3000
FMALE
33239
102
-------
Collection Site
Date
Species*
Length (mm)
Weight (g)
Sex
LABID"
Pickwick Reservoir
TRM259
9
23
93
CHC
552
1555
FMALE
33223
TRM259
9
23
93
CHC
414
525
MALE
33223
TRM259
9
23
93
CHC
461
790
FMALE
33223
TRM259
9
23
93
CHC
440
595
MALE
33223
TRM259
9
24
93
CHC
556
1550
FMALE
33223
Wheeler Reservoir
TRM277
9
30
93
CHC
468
965
FMALE
33225
TRM277
9
30
93
CHC
473
950
FMALE
33225
TRM277
9
30
93
CHC
498
870
FMALE
33225
TRM277
9
30
93
CHC
491
990
FMALE
33225
TRM277
9
30
93
CHC
396
475
FMALE
33225
TRM296
12
7
93
CHC
438
1065
FMALE
33228
TRM296
12
8
93
CHC
510
1850
FMALE
33228
TRM296
12
8
93
CHC
520
1725
FMALE
33228
TRM296
12
8
93
CHC
550
1775
FMALE
33228
TRM296
12
8
93
CHC
572
2045
FMALE
33228
TRM346
9
30
93
CHC
470
973
MALE
33230
TRM346
9
30
93
CHC
430
774
Id
33230
TRM346
9
30
93
CHC
503
1330
FMALE
33230
TRM 346
9
30
93
CHC
444
904
FMALE
33230
TRM346
9
30
93
CHC
648
3289
FMALE
33230
Elk River
ERM41
6
29
93
CHC
437
832
c
32551
ERM41
6
29
93
CHC
599
2592
c
32551
ERM41
6
29
93
CHC
349
278
c
32551
ERM41
6
29
93
CHC
347
344
c
32551
ERM41
6
29
93
CHC
295
228
c
32551
ERM41
6
29
93
LMB
495
2230
c
32552
ERM41
6
29
93
LMB
375
858
c
32552
ERM41
6
29
93
LMB
325
526
c
32552
ERM41
6
29
93
LMB
295
334
c
32552
103
-------
Collection Site
Date Species* Length (mm) Weight (g) Sex LABIDb
Sequatchie River
SEQRM7.1
6
22
93
CHC
503
1156
c
32555
SEQRM 7.1
6
22
93
CHC
482
1072
c
32555
SEQRM 7.1
6
22
93
CHC
381
496
c
32555
SEQRM 7.1
7
28
93
CHC
489
934
c
32555
SEQRM 7.1
7
28
93
CHC
437
648
c
32555
SEQRM 7.1
7
28
93
LMB
345
682
c
32557
SEQRM 7.1
6
22
93
SPB
231
174
c
32558
Hiwassee River
HIRM38
5
27
93
CHC
435
751
c
32559
HIRM38
6
4
93
CHC
346
381
c
32559
HIRM 38
7
19
93
CHC
492
1216
c
32559
HIRM 38
7
19
93
CHC
491
1456
c
32559
HIRM 38
7
19
93
CHC
541
1914
c
32559
HIRM 38
5
20
93
LMB
403
865
c
32562
HIRM 38
5
20
93
LMB
346
644
c
32562
HIRM 38
7
19
93
LMB
294
304
c
32562
HIRM 38
7
19
93
LMB
320
480
c
32562
HIRM 38
7
19
93
LMB
372
648
c
32562
Hiwassee Reservoir
HIRM 77
9
23
93
CHC
380
918
FMALE
33240
HIRM 77
10
21
93
CHC
463
692
MALE
33240
HIRM 77
10
21
93
CHC
569
1767
MALE
33240
HIRM 77
10
21
93
CHC
509
1100
FMALE
33240
HIRM 77
10
21
93
CHC
328
234
I"
33240
HIRM 77
9
23
93
LMB
395
848
FMALE
33411
HIRM 77
9
23
93
LMB
357
577
FMALE
33413
HIRM 77
9
23
93
LMB
351
594
MALE
33416
HIRM 77
9
23
93
LMB
340
511
FMALE
33417
HIRM 85
9
22
93
CHC
554
1669
MALE
33241
HIRM 85
9
22
93
CHC
474
932
MALE
33241
HIRM 85
9
22
93
CHC
383
396
MALE
33241
HIRM 85
9
21
93
CHC
470
877
MALE
33241
HIRM 85
9
21
93
CHC
381
386
MALE
33241
HIRM 85
9
22
93
LMB
380
874
FMALE
33418
HIRM 85
9
22
93
LMB
370
732
FMALE
33419
HIRM 85
9
22
93
LMB
345
545
FMALE
33420
HIRM 85
9
22
93
LMB
344
589
MALE
33421
HIRM 85
9
23
93
LMB
433
1214
FMALE
33422
104
-------
Collection Site
Date Species* Length (mm) Weight (g) Sex LABIDb
Chatuee Reservoir
HIRM 122
11 9
93
CHC
443
711
FMALE
32246
HIRM 122
11 9
93
CHC
491
961
MALE
32246
HIRM 122
11 9
93
CHC
483
963
MALE
32246
HIRM 122
11 9
93
CHC
422
667
FMALE
32246
HIRM 122
11 9
93
CHC
472
948
FMALE
32246
HIRM 122
11 9
93
LMB
484
1255
FMALE
33423
HIRM 122
11 9
93
LMB
365
610
FMALE
33299
HIRM 122
11 9
93
LMB
424
839
FMALE
33299
HIRM 122
11 9
93
LMB
388
725
FMALE
33299
HIRM 122
11 9
93
LMB
355
482
FMALE
33299
OCRM 12
11 11
93
CHC
410
664
FMALE
33251
OCRM 12
11 11
93
CHC
429
623
FMALE
33251
OCRM 12
11 11
93
CHC
545
1738
MALE
33251
OCRM 12
11 11
93
CHC
448
871
FMALE
33251
OCRM 12
11 11
93
CHC
398
398
FMALE
33251
OCRM 16
11 18
93
CHC
524
1198
MALE
33253
OCRM 16
11 18
93
CHC
452
736
FMALE
33253
OCRM 16
11 18
93
CHC
622
2488
MALE
33253
OCRM 16
11 19
93
CHC
510
1185
MALE
33253
OCRM 16
11 19
93
CHC
506
1041
FMALE
33253
Nottlev Reservoir
NOTRM 24
11 11
93
CHC
565
1778
FMALE
33248
NOTRM 24
11 11
93
CHC
553
1594
FMALE
33248
NOTRM 24
11 11
93
CHC
430
512
I"
33248
NOTRM 24
11 11
93
CHC
541
1412
MALE
33248
NOTRM 24
11 11
93
CHC
620
2163
MALE
33248
NOTRM 24
11 10
93
LMB
547
2424
FMALE
33424
NOTRM 24
11 10
93
LMB
453
1287
FMALE
33300
NOTRM 24
11 10
93
LMB
484
1619
FMALE
33300
NOTRM 24
11 10
93
LMB
386
926
MALE
33300
NOTRM 24
11 10
93
LMB
359
546
MALE
33300
105
-------
Collection Site Date Species" Length (mm) Weight (g) Sex LABIDb
Blue Ridge Reservoir
TOCRM 54
8
24
93
CHC
410
532
FMALE
33256
TOCRM 54
8
24
93
CHC
472
855
MALE
33256
TOCRM 54
8
24
93
CHC
487
974
MALE
33256
TOCRM 54
8
24
93
CHC
620
2068
MALE
33256
TOCRM 54
8
24
93
CHC
586
2113
FMALE
33256
TOCRM 54
8
24
93
LMB
360
668
MALE
33301
TOCRM 54
8
24
93
LMB
358
578
MALE
33301
TOCRM 54
8
24
93
LMB
323
491
Id
33301
TOCRM 54
8
24
93
LMB
331
520
FMALE
33301
TOCRM 54
8
24
93
LMB
417
912
FMALE
33301
Emorv River
EMORY RM 14.6
6
14
93
CHC
377
352
c
32569
EMORY RM 14.6
6
15
93
CHC
454
946
c
32569
EMORY RM 14.6
6
15
93
CHC
439
962
c
32569
EMORY RM 14.6
7
13
93
CHC
595
1838
c
32569
EMORY RM 14.6
7
13
93
CHC
375
536
c
32569
EMORY RM 14.6
6
14
93
LMB
295
390
c
32570
EMORY RM 14.6
6
15
93
LMB
414
992
c
32570
EMORY RM 14.6
6
15
93
LMB
445
1490
c
32570
EMORY RM 14.6
6
15
93
LMB
399
1032
c
32570
EMORY RM 14.6
6
15
93
LMB
327
478
c
32570
Norris Reservoir
CRM 80
11
5
93
CHC
435
756
FMALE
33258
CRM 80
11
5
93
CHC
455
806
FMALE
33258
CRM 80
11
5
93
CHC
369
432
FMALE
33258
CRM 80
11
5
93
CHC
373
422
MALE
33258
CRM 80
11
5
93
CHC
368
442
MALE
33258
CRM 80
11
11
93
LMB
416
932
MALE
33302
CRM 80
11
11
93
LMB
332
468
MALE
33302
CRM 80
11
23
93
LMB
470
1438
FMALE
33451
CRM 80
11
23
93
LMB
395
876
MALE
33302
CRM 80
11
23
93
LMB
365
660
MALE
33302
CRM 125
11
10
93
CHC
464
772
MALE
33261
CRM 125
11
10
93
CHC
453
844
MALE
33261
CRM 125
11
11
93
CHC
512
1246
MALE
33261
CRM 125
11
11
93
CHC
495
1242
MALE
33261
CRM 125
11
11
93
CHC
450
806
MALE
33261
106
-------
Collection Site Date Species* Length (mm) Weight (g) Sex LABID'
CRM 125
11 12
93
LMB
418
948
FMALE
33305
CRM 125
11 12
93
LMB
385
902
FMALE
33305
CRM 125
11 12
93
LMB
387
848
MALE
33305
CRM 125
11 12
93
LMB
397
866
FMALE
33305
CRM 125
11 12
93
LMB
376
864
MALE
33305
PRM30
11 9
93
CHC
531
1244
FMALE
33262
PRM30
11 9
93
CHC
554
1644
MALE
33262
PRM30
11 9
93
CHC
559
1502
MALE
33262
PRM30
11 9
93
CHC
512
1224
FMALE
33262
PRM30
11 9
93
CHC
461
724
MALE
33262
PRM30
11 9
93
LMB
353
528
FMALE
33307
PRM30
11 15
93
LMB
387
856
FMALE
33307
PRM30
11 15
93
LMB
441
1106
FMALE
33307
PRM30
11 15
93
LMB
401
828
FMALE
33307
PRM30
11 15
93
LMB
403
956
FMALE
33307
PRM30
11 15
93
LMB
385
704
MALE
33307
Clinch River
CRM 172
5
17
93
CHC
519
2035
FMALE
32573
CRM 172
5
17
93
CHC
473
1270
MALE
32573
CRM 172
5
17
93
CHC
520
1521
FMALE
32573
CRM 172
5
17
93
CHC
521
1628
MALE
32573
CRM 172
5
17
93
CHC
449
805
FMALE
32573
CRM 172
5
17
93
SMB
365
637
FMALE
32575
CRM 172
5
17
93
SMB
285
308
FMALE
32575
CRM 172
5
18
93
SMB
330
425
FMALE
32575
CRM 172
5
18
93
SMB
329
439
MALE
32575
CRM 172
5
18
93
SMB
234
171
FMALE
32575
Powell River
PRM 65.27
6
3
93
CHC
518
1642
FMALE
32576
PRM 65.27
6
3
93
CHC
595
2155
FMALE
32576
PRM 65.27
6
3
93
CHC
439
816
FMALE
32576
PRM 65.27
6
3
93
CHC
439
812
FMALE
32576
PRM 65.27
6
3
93
CHC
375
483
FMALE
32576
PRM 65.27
6
3
93
SMB
275
296
FMALE
32579
PRM 65.27
6
3
93
SMB
259
261
FMALE
32579
PRM 65.27
6
3
93
SMB
240
161
FMALE
32579
PRM 65.27
6
22
93
SMB
240
188
MALE
32579
PRM 65.27
6
22
93
SMB
303
352
FMALE
32579
107
-------
Collection Site
Date Species* Length (mm) Weight (g) Sex LABIDb
Tellico Reservoir
LTRM 1.0
10
93
CHC
569
1968
FMALE
33233
LTRM 1.0
10
93
CHC
579
2094
MALE
33233
LTRM 1.0
10
93
CHC
518
1150
FMALE
33233
LTRM 1.0
10
93
CHC
495
1138
MALE
33233
LTRM 1.0
10
93
CHC
423
594
FMALE
33233
LTRM 1.0
10
93
LMB
435
1185
FMALE
33447
LTRM 1.0
10
93
LMB
409
1042
FMALE
33290
LTRM 1.0
10
93
LMB
355
694
FMALE
33290
LTRM 1.0
10
93
LMB
357
540
MALE
33290
LTRM 1.0
10
93
LMB
333
478
FMALE
33290
LTRM 15
10
93
CHC
605
2086
MALE
33235
LTRM 15
10
93
CHC
589
1932
FMALE
33235
LTRM 15
10
93
CHC
519
1152
MALE
33235
LTRM 15
10
93
CHC
476
1148
FMALE
33235
LTRM 15
10
93
CHC
439
688
MALE
33235
LTRM 15
10
93
LMB
312
428
MALE
33292
LTRM 15
10
93
LMB
442
1122
FMALE
33292
LTRM 15
10
93
LMB
432
1280
FMALE
33448
LTRM 15
10
93
LMB
325
402
MALE
33292
LTRM 15
10
93
LMB
395
898
FMALE
33292
Fontana Reservoir
LTRM 62
11 18
93
CHC
505
1198
MALE
33263
LTRM 62
11 18
93
CHC
459
784
MALE
33263
LTRM 62
11 18
93
CHC
505
1076
MALE
33263
LTRM 62
11 18
93
CHC
421
514
MALE
33263
LTRM 62
11 18
93
LMB
445
1352
FMALE
33449
LTRM 62
11 18
93
LMB
374
858
MALE
33310
LTRM 62
11 18
93
LMB
350
814
MALE
33310
LTRM 62
11 18
93
LMB
341
670
MALE
33310
LTRM 62
11 18
93
LMB
368
800
MALE
33310
LTRM 81
11 16
93
CHC
471
842
MALE
33264
LTRM 81
11 16
93
CHC
397
419
FMALE
33264
LTRM 81
11 16
93
CHC
476
897
MALE
33264
LTRM 81
11 16
93
CHC
480
913
MALE
33264
LTRM 81
11 16
93
CHC
500
1015
MALE
33264
LTRM 81
11 16
93
LMB
356
716
MALE
33311
LTRM 81
11 16
93
LMB
383
977
FMALE
33311
LTRM 81
11 16
93
LMB
340
637
MALE
33311
108
-------
Collection Site
Date
Species"
Length (mm)
Weight (g)
Sex
LABED
LTRM 81
11 16
93
LMB
347
539
FMALE
33311
LTRM 81
11 16
93
LMB
300
346
MALE
33311
TUCKRM 3
11 17
93
CHC
497
1286
FMALE
33269
TUCKRM 3
11 17
93
CHC
567
1760
MALE
33269
TUCKRM 3
11 17
93
CHC
413
490
MALE
33269
TUCKRM 3
11 17
93
CHC
409
468
FMALE
33269
TUCKRM 3
11 17
93
CHC
374
378
MALE
33269
TUCKRM 3
11 17
93
LMB
549
2774
FMALE
33450
TUCKRM 3
11 17
93
LMB
374
790
FMALE
33312
TUCKRM 3
11 17
93
LMB
353
584
FMALE
33312
TUCKRM 3
11 17
93
LMB
309
434
FMALE
33312
TUCKRM 3
11 17
93
LMB
329
490
MALE
33312
Little Tennessee River
LTRM 94.77
LTRM 94.77
LTRM 94.77
LTRM 94.77
LTRM 94.77
LTRM 94.77
LTRM 94.77
LTRM 94.77
LTRM 94.77
LTRM 94.77
French Broad River
FBRM 77.5
FBRM 77.5
FBRM 77.5
FBRM 77.5
FBRM 77.5
FBRM 77.5
FBRM 77.5
FBRM 77.5
FBRM 77.5
6
2
93
CHC
392
645
FMALE
32580
6
2
93
CHC-
498
1160
FMALE
32580
6
2
93
CHC
425
594
FMALE
32580
6
2
93
CHC
375
456
FMALE
32580
6
2
93
CHC
399
587
FMALE
32580
15
93
SMB
352
562
^ALE
32582
15
93
SMB
289
352
c
32582
15
93
SMB
295
312
c
32582
15
93
SMB
285
280
c
32582
15
93
SMB
220
128
c
32582
6
24
93
CHC
494
1124
c
32591
6
24
93
CHC
393
488
c
32591
6
24
93
CHC
377
464
c
32591
14
93
CHC
405
454
c
32591
14
93
CHC
595
1764
c
32591
14
93
LMB
440
1334
c
32593
14
93
LMB
276
300
c
32593
14
93
SMB
380
940
c
32594
14
93
SMB
359
754
c
32594
109
-------
Collection Site Date Species' Length (mm) Weight (g) Sex LABIDb
Nolichuckv River
NRM8.5
6
7
93
C
672
5305
c
32583
NRM8.5
6
7
93
C
585
2925
c
32583
NRM8.5
6
7
93
C
638
3750
c
32583
NRM8.5
6
7
93
C
490
1765
c
32583
NRM8.5
6
18
93
C
685
3692
c
32583
NRM8.5
6
7
93
SPB
365
736
c
32586
NRM8.5
6
18
93
SPB
226
182
c
32586
NRM8.5
6
18
93
SPB
199
102
c
32586
NRM8.5
6
18
93
SPB
290
364
c
32586
Cherokee Reservoir
HRM53
10
29
93
CHC
557
1672
MALE
33271
HRM53
10
29
93
CHC
520
1262
MALE
33271
HRM53
10
29
93
CHC
493
1080
MALE
33271
HRM53
10
29
93
CHC
518
1046
MALE
33271
HRM53
10
29
93
CHC
438
746
FMALE
33271
HRM53
10
28
93
LMB
376
772
MALE
33313
HRM53
10
28
93
LMB
378
812
FMALE
33313
HRM53
10
28
93
LMB
372
670
MALE
33313
HRM53
10
28
93
LMB
342
560
FMALE
33313
HRM53
10
28
93
LMB
302
340
FMALE
33313
HRM75
11
17
93
CHC
510
1378
MALE
33274
HRM75
11
17
93
CHC
512
1478
FMALE
33274
HRM 75
11
17
93
CHC
509
1328
MALE
33274
HRM75
11
17
93
CHC
403
696
FMALE
33274
HRM 75
11
17
93
CHC
425
702
FMALE
33274
HRM 75
10
29
93
LMB
424
1228
FMALE
33314
HRM 75
10
29
93
LMB
512
1972
FMALE
33428
HRM 75
10
29
93
LMB
388
920
MALE
33314
HRM 75
10
29
93
LMB
351
670
MALE
33314
HRM 75
10
29
93
LMB
337
556
FMALE
33314
HRM 91
10
28
93
CHC
676
3698
MALE
33276
HRM 91
10
28
93
CHC
543
1716
FMALE
33276
HRM 91
10
28
93
CHC
459
974
MALE
33276
HRM 91
10
28
93
CHC
487
908
MALE
33276
HRM 91
10
28
93
CHC
392
478
FMALE
33276
-------
Collection Site
Date
Species*
Length (mm)
Weight (g)
Sex
LABIDb
HRM91
10
28
93
LMB
435
1194
FMALE
33430
HRM91
10
28
93
LMB
414
1098
FMALE
33315
HRM91
10
28
93
LMB
385
802
FMALE
33315
HRM91
10
28
93
LMB
340
542
FMALE
33315
HRM91
10
28
93
LMB
331
512
FMALE
33315
Holston River
HRM 109.9
6
14
93
LMB
412
926
C
32599
HRM 109.9
6
14
93
LMB
383
830
c
32599
HRM 109.9
6
14
93
LMB
325
438
c
32599
HRM 109.9
6
14
93
LMB
285
332
c
32599
HRM 109.9
6
15
93
LMB
430
1066
c
32599
HRM 109.9
6
15
93
CHC
536
1800
c
32597
HRM 109.9
6
15
93
CHC
593
3274
c
32597
HRM 109.9
6
15
93
CHC
563
2136
c
32597
HRM 109.9
6
15
93
CHC
468
1148
c
32597
HRM 109.9
6
15
93
CHC
563
1970
c
32597
Fort Patrick Henry Reservoir
SFHRM 9
10
12
93
CHC
569
1418
c
33279
SFHRM 9
10
12
93
CHC
547
1562
c
33279
SFHRM 9
10
12
93
CHC
519
1344
c
33279
SFHWvI 9
10
12
93
CHC
495
1065
c
33279
SFHRM 9
10
1
93
LMB
489
2040
FMALE
33316
SFHRM 9
10
1
93
LMB
385
960
MALE
33433
SFHRM 9
10
1
93
LMB
401
1040
MALE
33316
SFHRM 9
10
1
93
LMB
373
858
MALE
33316
SFHRM 9
10
1
93
LMB
344
574
FMALE
33316
111
-------
Collection Site Date Species* Length (mm) Weight (g) Sex LABE)b
Boone Reservoir
SFHRM 19
9
28
93
CHC
524
1190
MALE
33281
SFHRM 19
9
28
93
CHC
378
404
MALE
33281
SFHRM 19
9
28
93
CHC
368
348
FMALE
33281
SFHRM 19
9
28
93
CHC
381
368
FMALE
33281
SFHRM 19
9
28
93
CHC
411
480
FMALE
33281
SFHRM 19
9
28
93
LMB
421
1106
FMALE
33317
SFHRM 19
9
28
93
LMB
453
1362
FMALE
33434
SFHRM 19
9
28
93
LMB
435
1188
FMALE
33317
SFHRM 19
9
28
93
LMB
403
852
FMALE
33317
SFHRM 19
9
28
93
LMB
402
906
FMALE
33317
SFHRM 27
9
30
93
CHC
582
1926
FMALE
33284
SFHRM 27
9
30
93
CHC
939
1520
FMALE
33284
SFHRM 27
9
30
93
CHC
463
834
FMALE
33284
SFHRM 27
9
30
93
CHC
405
484
MALE
33284
SFHRM 27
9
30
93
CHC
437
664
FMALE
33435
SFHRM 27
9
30
93
LMB
463
1720
MALE
33435
SFHRM 27
9
30
93
LMB
474
1252
FMALE
33320
SFHRM 27
9
30
93
LMB
372
742
MALE
33320
SFHRM 27
9
30
93
LMB
379
740
MALE
33320
SFHRM 27
9
30
93
LMB
343
568
FMALE
33320
WRM 7
9
29
93
CHC
588
2000
MALE
33285
WRM 7
9
29
93
CHC
1604
1604
FMALE
33285
WRM 7
9
29
93
CHC
1114
1114
FMALE
33285
WRM 7
9
29
93
CHC
854
854
MALE
33285
WRM 7
9
29
93
CHC
458
458
MALE
33285
WRM 7
9
29
93
LMB
412
1046
FMALE
33322
WRM 7
9
29
93
LMB
486
1636
FMALE
33436
WRM 7
9
29
93
LMB
392
922
MALE
33322
WRM 7
9
29
93
LMB
393
992
FMALE
33322
WRM 7
9
29
93
LMB
336
566
MALE
33322
112
-------
Collection Site Date Species" Length (mm) Weight (g) Sex LABIDb
Watauea Reservoir
WRM37
11
5
93
CHC
645
2644
FMALE
33286
WRM37
11
5
93
CHC
620
2126
FMALE
33286
WRM37
11
5
93
CHC
581
2190
FMALE
33286
WRM37
11
5
93
CHC
508
970
MALE
33286
WRM37
11
5
93
CHC
421
530
FMALE
33286
WRM37
11
5
93
LMB
495
2276
FMALE
33437
WRM37
11
5
93
LMB
450
1418
FMALE
33325
WRM37
11
5
93
LMB
420
1258
FMALE
33325
WRM37
11
5
93
LMB
410
1068
FMALE
33325
WRM37
11
5
93
LMB
392
988
FMALE
33325
South Holston Reservoir
SFHRM5I
11
2
93
CHC
570
1718
MALE
33287
SFHRM51
11
2
93
CHC
517
1398
FMALE
33287
SFHRM51
12
8
93
CHC
631
2984
MALE
33287
SFHRM51
12
8
93
CHC
435
718
FMALE
33287
SFHRM51
12
8
93
CHC
533
998
MALE
33287
SFHRM51
11
2
93
LMB
390
940
FMALE
33326
SFHRM 51
11
2
93
LMB
469
1572
FMALE
33438
SFHRM 51
11
2
93
LMB
447
1412
FMALE
33326
SFHRM 51
11
2
93
LMB
415
764
MALE
33326
SFHRM 51
12
8
93
LMB
397
758
MALE
33326
a CHC = channel catfish, SPB = spotted bass, LMB = largemouth bass,. SMB = smallmouth bass
b LAB ID = number assigned by TVA's Environmental Chemistry Laboratory. It is used to link laboratory
analysis data with physical data from fish.
c Observations on sex and external and internal characteristics of these fish were lost because of an error in
a prototype computer program.
d I = immature (sex could not be determined).
113
-------
Table A. 2 Concentrations (ng/g) of organics in composited fish samples from stream and reservoir monitoring locations, 1993.
Collection Site
Species'
LABID"
% LIPIDS
PCBs
MIREX
TOXAPH
HEPTA
ALDRIN
BENZ
DDTr
DIELD
ENDO
ENDRIN
CHLOF
Duck River
DRM 22.5
DRM 22 5
CHC
SPB
32548
32550
2.3
0.1
0.1
<0.1
<0.008
<0.008
0.5
0 5
<0.01
<0 01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0 01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
Bear Creek Reservoir
BCM 75
CHC
33238
2.9
<0.1
<0.008
<0.5
<0.01
<0.01
<0.01
0.06
<0.01
<0.01
<0.01
<0.01
Little Bear Creek Resen'oir
LBCRM 12
CHC
33239
3.1
<0.1
<0.008
<0.5
<0 01
<0.01
<0.01
0.02
<0.01
<0.01
<0.01
<0.01
Pickwick Reservoir
TRM 259
CHC
33223
3.8
0.5
<0.008
<0.5
<0.01
<0.01
<0.01
0.41
<0.01
<0.01
<0.01
0.04
Wheeler Reservoir
TRM 277
TRM 296
TRM 346
CHC
CHC
CHC
33225
33228
33230
2.8
6.9
8.3
0.5
08
1.4
<0.008
<0.008
<0.008
<0.5
<0.5
<0.5
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
0.57
1.06
0.73
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
0.07
0.16
0.15
Emory River
ERM41
ERM41
CHC
LMB
32551
32552
2.8
0.7
0.3
0.2
<0.008
<0.008
<0.5
<0.5
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
0.10
<0.01
<0.01
<0 01
<0.01
<0.01
<0.01
0.01
<0.01
Sequatchie River
SEQRM 7.1
SEQRM 7.1
SEQRM 7.1
CHC
LMB
SPB
32555
32557
32558
3.9
0.5
0.2
0.6
<0.1
<0.1
<0.008
<0.008
<0.008
<0.5
<0.5
<0.5
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
0.10
0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
0.03
0.01
<0.01
Hiwassee River
HIRM 38
HIRM38
CHC
LMB
32559
32562
8.4
1 6
0.7
<0.1
<0.008
<0.008
<0.5
<0.5
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
0.05
0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
0.05
0.01
114
-------
Collection Site Species' LABID" % LIPIDS PCBs MIREX TOXAPH HEPTA ALDRIN BENZ DDTr DIELD ENDO ENDRIN CHLOR
Hiwassee Reservoir
HIRM 77
HIRM 85
Chatuge Reservoir
HIRM 122
Nottley Reservoir
NOTRM 24
Ocoee t) 1
OCRM 12.5
OCRM 16
Blue Ridge Reservoir
TOCRM54
Emory River
EMORY RM 14.6
EMORY RM 14.6
Norris Reservoir
CRM 80
CRM 125
PRM30
Clinch River
CRM 172
CRM 172
Powell River
PRM 65.27
PRM 65.27
CHC 33240
CHC 33241
CHC 32246
CHC 33248
CHC 33251
CHC 33253
CHC 33256
CHC 32569
LMB 32570
CHC 33258
CHC 33261
CHC 33262
CHC 32573
SMB 32575
CHC 32576
SMB 32579
2.7 <0.1
1.4 <0.1
3.6 <0.1
2.0 <0.1
2.5 0.8
4.3 1.0
1.4 <0.1
4.2 0.8
1.9 0.2
6.3 0.2
2.5 0.2
3.8 0.2
6.6 <0.1
0.4 <0.1
3.5 <0.1
0.8 <0.1
<0.008 <0.5
<0.008 <0 5
<0.008 <0.5
<0.008 <0.5
<0.008 <0.5
<0.008 <0.5
<0.008 <0.5
<0.008 <0.5
<0.008 <0.5
<0.008 <0.5
<0.008 <0 5
<0.008 <0.5
<0.008 <0.5
<0.008 <0.5
<0.008 <0.5
<0.008 <0.5
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 0.02
<0.01 0.01
<0.01 0.04
<0.01 0.15
<0.01 0.05
<0.01 0.07
<0.01 0.06
<0.01 0.07
<0.01 0.01
<0.01 0.06
<0.01 0.06
<0.01 0.05
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0 01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 0.02
<0.01 0.02
<0.01 <0.01
<0.01 0.05
<0.01 0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
<0.01 <0.01
-------
Collection Site Species' LABID' % LIPIDS PCBs MIREX TOXAPH
Tellico Reservoir
LTRM 1.0
LTRM 15
Fontana Reservoir
LTRM 62
LTRM 81
TUCKRM 3
Little Tennessee River
LTRM 94.77
LTRM 94.77
French Broad River
FBRM 77.3
FBRM 77.5
Nolichucky River
NRM 8.5
NRM 8.5
Cherokee Reservoir
HRM53
HRM 75
HRM91
Holston River
HRM 109.9
HRM 109.9
Fork Patrick Henry Reservoir
SFHRM 9
CHC
33233
3.3
1.4
<0.008
<0.5
CHC
33235
3.7
1.0
<0.008
<0.5
CHC
33263
1.9
<0.1
<0.008
<0.5
CHC
33264
2.3
0.4
<0.008
<0.5
CHC
33269
2.7
0.1
<0.008
<0.5
CHC
32580
5.2
<0.1
<0.008
<0.5
SMB
32580
0.5
<0.1
<0.008
<0.5
CHC
32591
1.9
<0.1
<0.008
<0.5
SMB
32594
1.2
<0.1
<0.008
<0.5
C
32583
2.1
<0.1
<0.008
<0.5
SPB
32586
0 5
<0.1
<0.008
<05
CHC
33271
7.4
0.3
<0.008
<0.5
CHC
33274
3.0
<0.1
<0.008
<0.5
CHC
33276
4.2
0.6
<0.008
<0.5
CHC
32597
4.7
<0.1
<0.008
<0.5
LMB
32599
0.2
<0.1
<0.008
<0.5
CHC
33279
2.7
0.2
<0.008
<0.5
116
HEPTA ALDRIN BENZ DDTr DIELD ENDO ENDRIN CHLOR
<0.01
<0 01
<0.01
0.10
<0.01
<0.01
<0.01
0.06
<0.01
<0.01
<0.01
0.06
<0.01
<0.01
<0.01
0.04
<0.01
<0.01
<0.01
0.04
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
0.06
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
0.06
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0 01
<0 01
<0.01
<0.01
<0.01
<0.01
<0 01
<0 01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0 01
<0 01
<0.01
<0.01
<0 01
<0 01
<0.01
<0.01
<0.01
<0.01
0.06
<0.01
<0.01
<0.01
0.11
<0.01
<0.01
<0.01
0.05
<0 01
<0.01
<0.01
0.04
<0.01
<0.01
<0.01
0.06
<0.01
<0.01
<0.01
0.15
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
0.03
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
0.05
<0.01
<0.01
<0.01
<0.01
-------
Collection Site
Specie.,
LABID"
% LIPIDS
PCBs
MIREX
TOXAPH 1
UEPTA
ALDRIN
BENZ
DDTr
DIELD
ENDO
ENDRIN
CHLOR
Boone Reservoir
SFHRM 19
CHC
33281
2.6
0.7
<0.008
<0.5
<0.01
<0.01
<0.01
0.06
<0.01
<0.01
<0.01
0.02
SFHRM 27
CHC
33284
5.0
0.5
<0.008
<0.5
<0.01
<0.01
<0.01
0.06
<0.01
<0.01
<0.01
<0.01
WRM 6.5
CHC
33285
3.1
0.4
<0.008
<0.5
<0.01
<0.01
<0.01
0.06
<0.01
<0.01
<0.01
<0.01
Watauga Reservoir
WRM 37.4
CHC
33286
6.8
0.1
<0.008
<0.5
<0.01
<0.01
<0.01
0.1
<0.01
<0.01
<0.01
<0.01
South Holston Reservoir
SFHRM 51
CHC
33287
6.0
0.2
<0.008
<0.5
<0.01
<0.01
<0.01
0.08
<0.01
<0.01
<0.01
<0.01
a CHC = channel catfish, SPB = spotted bass,
LMB =
largemouth bass, SMB
= smallmouth bass
LABID = number assigned by TVA's Environmental Chemistry Laboratory. It is used to link laboratory analysis data with physical data from fish.
117
-------
Table A-3 Concentrations (|ig/g) of metals in composited fish flesh samples from stream and
reservoir monitoring locations, 1993.
Collection Site
Species'
LABID"
As
Cd
Pb
Hg
Se
Duck River
DRM 22.5
CHC
32548
<0.1
<0.05
<0.02
<0.1
0.2
DRM22.5
SPB
32550
<0.1
<0.05
<0.02
<0.1
0.2
Bear Creek Reservoir
BCM75
CHC
33238
<0.1
<0.05
0.02
0.66
0.2
BCM 75
LMB
33295
0.71
Little Bear Creek Reservoir
LBCRM 12
LMB
33296
0.60
LBCRM 12
CHC
33239
<0.1
<0.05
<0.02
0.22
<0.2
Pickwick Reservoir
TRM259
CHC
33223
<0.1
<0.05
0.02
0.12
<0.2
Wheeler Reservoir
TRM277
CHC
33225
<0.1
<0.05
0.02
0.13
<0.2
TRM 296
CHC
33228
<0.1
<0.05
0.05
<0.1
<0.2
TRM346
CHC
33230
0.12
<0.05
<0.02
<0.1
<0.2
Elk River
ERM41
CHC
32551
<0.1
<0.05
<0.02
<0.1
<0.2
ERM41
LMB
32552
<0.1
<0.05
<0.02
0.31
0.2
Sequatchie River
SEQRM 7.1
CHC
32555
<0.1
<0.05
<0.02
0.13
<0.2
SEQRM 7.1
LMB
32557
<0.1
<0.05
<0.02
0.35
0.3
SEQRM 7.1
SPB
32558
<0.1
<0.05
0.24
0.63
0.3
Hiwassee River
HIRM 38
CHC
32559
<0.1
<0.05
<0.02
0.17
<0.2
HIRM 38
LMB
32562
<0.1
<0.05
<0.02
0.26
0.3
Hiwassee Reservoir
HIRM 77
CHC
33240
<0.1
<0.05
0.03
0.54
0.2
HIRM 77
LMB
33297
0.33
HIRM 85
CHC
33241
<0.1
<0.05
0.02
0.40
<0.2
HIRM 85
LMB
33298
0.30
Chatuge Reservoir
HIRM 122
CHC
32246
<0.1
<0.05
<0.02
0.13
0.3
HIRM 122
LMB
33299
0.45
118
-------
Collection Site
Species'
LABID"
As
Cd
Pb
Hg
Se
Nottley Reservoir
NOTRM24
NOTRM24
CHC
LMB
33248
33300
<0.1
<0.05
0.16
0.60
0.44
<0.2
Ocoee #1
OCRM 12
OCRM 16
CHC
CHC
33251
33253
<0.1
<0.1
<0.05
<0.05
0.06
0.04
<0.1
<0.1
0.5
0.4
Blue Ridge Reservoir
TOCRM 54
TOCRM 54
CHC
LMB
33256
33301
<0.1
<0.05
<0.02
0.13
0.12
0.2
Emory River
EMORY RM 14.6
EMORY RM 14.6
CHC
LMB
32569
32569
<0.1
<0.1
<0.05
<0.05
<0.02
<0.02
0.51
0.40
<0.2
0.3
Norris Reservoir
CRM 80
CRM 80
CRM 125
CRM 125
PRM 30
PRM 30
CHC
LMB
CHC
LMB
CHC
LMB
33258
33302
33261
33305
33262
33307
<0.1
<0.1
<0.1
<0.05
<0.05
<0.05
0.15
0.02
<0.02
0.24
0.59
<0.1
0.24
<0.1
0.12
<0.2
<0.2
<0.2
Clinch River
CRM 172
CRM 172
CHC
SMB
32573
32575
<0.1
<0.1
<0.05
<0.05
<0.02
0.06
0.13
0.14
0.2
0.6
Powell River
PRM 65.27
PRM 65.27
CHC
SMB
32576
32579
<0.1
<0.1
<0.05
<0.05
<0.02
<0.02
<0.1
0.23
0.2
0.4
Tellico Reservoir
LTRM 1.0
LTRM 1.0
LTRM 15
LTRM 15
CHC
LMB
CHC
LMB
33233
33290
33235
33292
<0.1
<0.1
<0.05
<0.05
0.02
<0.02
0.56
0.15
0.29
0.22
<0.2
<0.2
Fontana Reservoir
LTRM 62
LTRM 62
LTRM 81
LTRM 81
TUCKRM 3
TUCKRM3
CHC
LMB
CHC
LMB
CHC
LMB
33263
33310
33264
33311
33269
33312
<0.1
<0.1
<0.1
<0.05
<0.05
<0.05
0.04
<0.02
0.06
0.30
0.18
0.43
0.18
0.38
0.32
<0.2
<0.2
<0.2
119
-------
Collection Site Species' LABIDb As Cd Pb Hg Se
Little Tennessee River
LTRM 94.77 CHC 32580 <0.1 <0.05 <0.02 0.27 <0.2
LTRM 94.77 LMB 32582 <0.1 <0.05 0.10 0.44 0.2
French Broad River
FBRM 77.5 CHC
FBRM 77.5 LMB
FBRM 77.5 SMB
32591 <0.1 <0.05
32593 <0.1 <0.05
32594 <0.1 <0.05
0.07 0.24 <0.2
<0.02 0.19 0.2
0.11 0.51 0.4
Nolichucky River
NRM8.5 C 32583 <0.1 <0.05 0.02 0.15 0.3
NRM8.5 SPB 32586 <0.1 <0.05 0.10 0.14 0.2
Cherokee Reservoir
HRM53
HRM 53
HRM 75
HRM 75
HRM 91
HRM 91
CHC
LMB
CHC
LMB
CHC
LMB
33271
33313
33274
33314
33276
33315
<0.1
<0.1
<0.1
<0.05
<0.05
<0.05
<0.02
<0.02
0.03
0.11
0.17
0.18
0.17
0.38
0.24
<0.2
<0.2
<0.2
Holston River
HRM 109.9
HRM 109.9
CHC
LMB
32597
32599
<0.1
<0.1
<0.05
<0.05
<0.02
0.08
<0.1
0.40
0.3
<0.2
Fork Patrick Henry Reservoir
SFHRM9 CHC 33279
SFHRM9 LMB 33316
<0.1
<0.05
<0.02
<0.1
<0.1
<0.2
Boone Reservoir
SFHRM 19
SFHRM 19
SFHRM 27
SFHRM 27
WRM7
WRM 7
CHC
LMB
CHC
LMB
CHC
LMB
33281
33317
33284
33320
33285
33322
<0.1
<0.1
<0.1
<0.05
<0.05
<0.05
0.15
<0.02
0.03
0.13
0.14
0.21
0.22
0.14
0.12
<0.2
<0.2
<0.2
Watauga Reservoir
WRM 38 CHC 33286 <0.1 <0.05 <0.02 0.48 <0.2
WRM 38 LMB
South Holston Reservoir
SFHRM 51 CHC 33287 <0.1 <0.05 0.18 0.47 <0.2
SFHRM 51 LMB 33326 0 45
a CHC - channel catfish, SPB = spotted bass, LMB = largemouth bass, SMB = smallmouth bass
b LABID = number assigned by TVA's Environmental Chemistry Laboratory. It is used to link laboratory analysis data with physical data
from fish.
120
-------
APPENDIX B
CHRONOLOGICAL LISTING OF TVA REPORTS
RELATING TO TOXICS IN FISH
NOTE: Copies of reports are available from:
Water Management Library
Tennessee Valley Authority
CST 16B
1101 Market Street
Chattanooga, TN 37402-2801
(615)751-7338
Fax: (615) 751-7479
121
-------
CHRONOLOGICAL LISTING OF TVA REPORTS
RELATING TO TOXICS IN FISH
MONITORING OF MERCURY CONCENTRATIONS IN FISHES COLLECTED FROM PICKWICK
AND KENTUCKY RESERVOIRS MAY 1970 - FEBRUARY 1971 - April 1971
CONTROL AND CONFIDENCE INTERVAL CHARTS FOR MONITORING MERCURY
CONTAMINATION OF FISH - A. L. Jensen - June 1971
SUMMARY OF OCOEE RIVER WATER QUALITY, SEDIMENT, AND BIOLOGICAL DATA
COLLECTED THROUGH SEPTEMBER 1975 - Ralph Brown and Dennis Meinert
I-WQ-76-1 - May 1976
EVALUATION OF THE MERCURY MONITORING PROGRAM FROM THE NORTH FORK HOLSTON
RIVER - Thomas W. Toole and Richard Ruane - E-WQ-76-2 -
September 1976
TRENDS IN THE MERCURY CONTENT OF FISH FROM KENTUCKY, PICKWICK, AND
CHICKAMAUGA RESERVOIRS 1970-1977 - Jack Milligan - I-WQ-78-15 -
December 1978
ANALYSIS OF MERCURY DATA COLLECTED FROM THE NORTH FORK OF THE HOLSTON
RIVER - Jack Milligan and Richard Ruane - TVA/EP-78/12 -
December 1978
ENGINEERING AND ENVIRONMENTAL STUDY OF DDT CONTAMINATION HUNTSVILLE
SPRING BRANCH, INDIAN CREEK, AND ADJACENT LANDS AND WATERS, WHEELER
RESERVOIR, ALABAMA-TASK 1-DDT LEVELS IN IMPORTANT FISH SPECIES THROUGHOUT
WILSON, WHEELER, AND GUNTERS VILLE RESERVOIRS-Final Data Report - August 1980
ENGINEERING AND ENVIRONMENTAL STUDY OF DDT CONTAMINATION HUNTS VILLE
SPRING BRANCH, INDIAN CREEK, AND ADJACENT LANDS AND WATERS, WHEELER
RESERVOIR, ALABAMA-TASK 2 FISH POPULATION ESTIMATES AND DDT
CONCENTRATIONS IN YOUNG-OF-YEAR FISHES FROM INDIAN CREEK AND HUNTS VILLE
SPRING BRANCH EMBAYMENTS OF WHEELER RESERVOIR-Final Data Report - August 1980
ENGINEERING AND ENVIRONMENTAL STUDY OF DDT CONTAMINATION HUNTS VILLE
SPRING BRANCH, INDIAN CREEK, AND ADJACENT LANDS AND WATERS, WHEELER
RESERVOIR, ALABAMA-TASK 3-ASSESSMENT OF DDT CONCENTRATIONS IN SEDIMENTS
CORRESPONDING TO ARE A-WIDE FISHERIES STUDIES-Final Data Report - August 1980
ENGINEERING AND ENVIRONMENTAL STUDY OF DDT CONTAMINATION HUNTS VILLE
SPRING BRANCH, INDIAN CREEK, AND ADJACENT LANDS AND WATERS, WHEELER
RESERVOIR, ALABAMA-TASK 4-ASSESSMENT OF DDT CONCENTRATIONS AND OTHER
CONTAMINANTS IN SEDIMENTS IN REDSTONE ARSENAL VICINITY-Final Data Report -
August 1980
122
-------
ENGINEERING AND ENVIRONMENTAL STUDY OF DDT CONTAMINATION HUNTSVILLE
SPRING BRANCH, INDIAN CREEK, AND ADJACENT LANDS AND WATERS, WHEELER
RESERVOIR, ALABAMA-TASK 5-AQUATIC BIOTRANSPORT (EXCLUDING
VERTEBRATES)-Final Data Report - August 1980
ENGINEERING AND ENVIRONMENTAL STUDY OF DDT CONTAMINATION HUNTSVILLE
SPRING BRANCH, INDIAN CREEK, AND ADJACENT LANDS AND WATERS, WHEELER
RESERVOIR, ALABAMA-TASK 6-Vol. 1-HYDROLOGIC AND SEDIMENT DATA-Final Data
Report - August 1980
ENGINEERING AND ENVIRONMENTAL STUDY OF DDT CONTAMINATION HUNTSVILLE
SPRING BRANCH, INDIAN CREEK AND ADJACENT LANDS AND WATERS, WHEELER
RESERVOIR, ALABAMA-TASK 6-Vol II-HYDROLOGICAL AND SEDIMENTOLOGICAL
CALCULATIONS-DATA ANALYSIS-Final Data Report - August 1980
ENGINEERING AND ENVIRONMENTAL STUDY OF DDT CONTAMINATION HUNTSVILLE
SPRING BRANCH, INDIAN CREEK AND ADJACENT LANDS AND WATERS, WHEELER
RESERVOIR, ALABAMA-TASK 6-Vol III-HYDROLOGICAL AND SEDIMENTOLOGICAL
CALCULATIONS-INPUT DATA-Final Data Report - August 1980
ENGINEERING AND ENVIRONMENTAL STUDY OF DDT CONTAMINATION HUNTSVILLE
SPRING BRANCH, INDIAN CREEK, AND ADJACENT LANDS AND WATERS, WHEELER
RESERVOIR, ALABAMA-TASK 7-ASSESSMENT OF DDT LEVELS OF SELECTED
VERTEBRATES IN AND ADJACENT TO WHEELER, WILSON, AND GUNTERSVILLE
RESERVOIRS (SPATIAL EXTENT OF CONTAMINATION)-Final Data Report - August 1980
ENGINEERING AND ENVIRONMENTAL STUDY OF DDT CONTAMINATION HUNTSVILLE
SPRING BRANCH, INDIAN CREEK, AND ADJACENT LANDS AND WATERS, WHEELER
RESERVOIR, ALABAMA-QUALITY ASSURANCE DOCUMENT-Final Data Report - August 1980
TRENDS IN THE.MERCURY CONCENTRATION IN LARGEMOUTH BASS, CARP, AND DRUM
FROM KENTUCKY AND PICKWICK RESERVOIRS 1970-1979 - Jack Milligan -
. TVA/ONR/WRF-83/4 - May 1983
POLY CHLORINATED BIPHENYL (PCB) CONCENTRATIONS IN CATFISH FROM FLEET
HOLLOW, WILSON RESERVOIR - Donald Dycus, Peter Hackney, and William Barr -
TVA/ONR/WRF-83/11 - May 1983
SUMMARY OF EXISTING WATER, SEDIMENT, FISH, AND SOIL DATA IN THE VICINITY
OF THE OAK RIDGE RESERVATION - August 1983
DETERMINATION OF THE RELATIONSHIP BETWEEN CONCENTRATION OF DDT IN SEDIMENT
AND CONCENTRATION OF DDT IN FISH FOR THE HSB-IC TRIBUTARY SYSTEM - January
1984
PHYSICAL, CHEMICAL, AND BIOLOGICAL PROCESSES AFFECTING THE UPTAKE AND
LOSS OF DDT BY FISH FROM DDT CONTAMINATED SEDIMENTS: REVIEW AND
EVALUATION OF LITERATURE PERTINENT TO HUNTSVILLE SPRING BRANCH-INDIAN
CREEK REMEDIAL ACTIONS - TVA/ONRED/AWR-84/9 - May 1984
ORGANIC COMPOUNDS AND METALS IN FISH FROM CHATTANOOGA CREEK AND NICKAJACK
RESERVOIR - Jack D. Milligan and Barney S. Neal - TVA/ONRED/AWR-85-1 - November 1984
123
-------
POLY CHLORINATED BIPHENYL CONTAMINATION OF FORT LOUDOUN RESERVOIR: A
MANAGEMENT RESPONSE TO THE FOOD AND DRUG ADMINISTRATION 1984 REVISION OF
LIMITS FOR PCB IN FISH FLESH - Neil Carriker and David McKinney -1985
INSTREAM CONTAMINANT STUDY - TASK 4 - FISH SAMPLING AND ANALYSIS -
Prepared for USDOE, Oak Ridge, Tennessee - TVA/ONRED/April 1985
WATER QUALITY IN OCOEE NO. 1 RESERVOIR-VOLUME 1: SUMMARY REPORT - Janice
Cox - TVA/ONRED/AWR-86/13 - January 1986
WATER QUALITY IN OCOEE NO. 1 RESERVOIR-VOLUME 2: TECHNICAL REPORT -
Janice Cox - TVA/ONRED/AWR-86/13 - January 1986
HEAVY METAL AND PCB CONCENTRATIONS IN SEDIMENTS FROM SELECTED TV A
RESERVOIRS - TVA/ONRED/AWR-86/35 - April 1986
NORTH ALABAMA WATER QUALITY ASSESSMENT: VOLUME VII-CONTAMINANTS IN BIOTA
- Donald Dycus - TVA/ONRED/AWR-86/33 - April 1986
PCB CONCENTRATIONS IN WILSON RESERVOIR CATFISH-1985 - Donald Dycus and
Donny Loweiy - TVA/ONRED/AWR-86/57 - September 1986
CONCENTRATIONS OF PCBs, DDTr, AND SELECTED METALS IN BIOTA FROM
GUNTERSVILLE RESERVOIR - Donald Dycus and Donny Lowery - TVA/ONRED/AWR-87/18 -
October 1986
NORTH ALABAMA WATER QUALITY ASSESSMENT: VOLUME X CONCENTRATIONS OF PCBs,
DDTr, AND SELECTED METALS IN CATFISH FROM WHEELER RESERVOIR - Donald Dycus
and Donny Lowery - October 1986
CONCENTRATIONS OF PCBs, DDTr, AND METALS IN FISH FROM TELLICO RESERVOIR -
Donald Dycus and Gary Hickman - TVA/ONRED/AWR-87/25 - November 1986
ESTIMATION OF THE BIOACCUMULATION OF MERCURY BY BLUEGILL SUNFISH IN EAST
FORK POPLAR CREEK-Final Report - Richard Young - April 1987
SCREENING FOR TOXICS IN BIOTA AND SEDIMENT FROM THE LOWER TENNESSEE RIVER
- John Jenkinson - TVA/ONR/AWR-87/34 - July 1987
PCB CONCENTRATIONS IN WILSON RESERVOIR CATTISH-1986 - Donald Dycus and
Donny Lowery - TVA/ONRED/AWR-88/2 - August 1987
NORTH ALABAMA WATER QUALITY ASSESSMENT: VOLUME 14-CONCENTRATIONS OF
PCBs, AND DDTr IN CATFISH FROM UPPER PICKWICK RESERVOIR AND PCBs FROM
WILSON RESERVOIR - Donald Dycus and Donny Lowery - TVA/ONRED/AWR 85/22 - September
1987
PCB CONCENTRATIONS IN FISH AND SEDIMENT FROM FORT LOUDOUN RESERVOIR-1985
- Donald Dycus, Joseph Fehring, and Gary Hickman - TVA/ONRED/AWR 88/8 - October 1987
SURFACE WATER MONITORING STRATEGY-AMBIENT MONITORING-RESULTS FROM
ANALYSES ON FISH TISSUE COLLECTED IN 1986 - Donald Dycus - May 1988
124
-------
PCB LEVELS IN FISH FROM FORT LOUDOUN RESERVOIR, FORT LOUDOUN DAM
TAILRACE, TELLICO RESERVOIR, AND CHILHOWEE RESERVOIR AUTUMN 1986 TO
WINTER 1987 - Donald Dycus and Gary Hickman - TVA/ONRED/AWR 88/19 - June 1988
LEVELS OF SELECTED METALS AND PCBs IN CHANNEL AND BLUE CATFISH FROM
CHICKAMAUGA RESERVOIR-1987 - Donald Dycus - July 1988
PCB CONCENTRATIONS IN WILSON RESERVOIR CATFISH-1987 - Donald Dycus and
Donny Lowery - August 1988
CONCENTRATIONS OF PCBs IN FISH AND SEDIMENTS FROM UPPER GUNTERSVILLE
RESERVOIR-1987 - Donald Dycus - TVA/WR/AB-89/4 - May 1989
RESULTS OF FISH TISSUE SCREENING STUDIES FROM SITES IN THE TENNESSEE AND
CUMBERLAND RIVERS-1987 - Donald Dycus - TVA/WR/AB-89/5 - May 1989
PCB STUDIES ON FISH FROM WATTS BAR, FORT LOUDOUN, TELLICO, AND CHILHOWEE
RESERVOIRS-1987 - Donald Dycus - TVA/WR7AB--89/10 - July 1989
LEVELS OF SELECTED METALS AND PCBs IN CHANNEL CATTISH FROM CHICKAMAUGA
RESERVOIR-1988 - Donald Dycus - TVA/WR/AB-90/3 - February 1990
RESULTS OF FISH TISSUE SCREENING STUDIES IN THE TENNESSEE AND CUMBERLAND
RIVERS IN 1988 - Donald Dycus - TVA/WR/AB-90/7 - July 1990
RESULTS OF PCB AND CHLORDANE ANALYSES ON FISH COLLECTED FROM NICKAJACK
RESERVOIR IN JANUARY AND FEBRUARY 1989 - Donald Dycus - TVA/WR/AB—90/9 - July 1990
PCB STUDIES ON FISH FROM WATTS BAR, FORT LOUDOUN, TELLICO, AND MELTON
HILL RESERVOIRS - 1988 - Donald Dycus - TVA/WR/AB—90/11 - September 1990
RESERVOIR MONITORING - 1990 - FISH TISSUE STUDIES IN THE TENNESSEE VALLEY
IN 1989 - Gordon E. Hall and Donald Dycus - TVA/WR/AB-91/12 - October 1991
RESERVOIR MONITORING - 1991 - FISH TISSUE STUDIES IN THE TENNESSEE VALLEY IN 1990 -
Joella A. Bates, Donald L. Dycus, and Gordon E. Hall - TVA/WR-92/7 - December 1992
RESERVOIR MONITORING - 1992 - FISH TISSUE STUDIES IN THE TENNESSEE VALLEY IN 1991
AND 1992 - Donald L. Williams and Donald L. Dycus - December 1993
RESERVOIR MONITORING - 1993 - FISH TISSUE STUDIES IN THE TENNESSEE VALLEY IN 1993 -
Donald L. Williams and Donald L. Dycus - July 1994
125
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APPENDIX C
RATIONALE AND PROCEDURES FOR COLLECTION, PROCESSING,
AND ANALYSIS OF FISH TISSUE SAMPLES
127
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Appendix C
RATIONALE AND PROCEDURES FOR COLLECTION. PROCESSING.
AND ANALYSIS OF FISH TISSUE SAMPLES
RATIONALE
All fish tissue studies are closely coordinated among TVA and various state agencies
to ensure all needs are met, avoid duplication of effort, and ensure efficient use of available
funds. Planning meetings are usually held in the summer followed by collection efforts in
autumn. In many cases efforts are combined so that one organization collects the fish and
another analyzes them. When more than one analytical laboratory is involved, samples are
split between the labs to allow comparison of results.
Several important decisions must be made in studies such as these. Should analyses
be conducted on fish composites or individual fish? Should whole fish or fillets be analyzed?
Should fillets have the skin on or off? Should the bellyflap (which is rich in lipids and
lipophilic contaminants) be left on the fillet or removed? These are all valid options and all
have been used in previous studies (McCracken 1983). Selection of specific protocols is
dependent upon the objective of the study.
Should analyses be conducted on fish composites or individual fish?—TVA's
approach differs between screening studies and intensive studies because the objectives of
those studies differ. Screening studies are intended to identify sites with potential problems,
whereas intensive studies are intended to define the extent of the problem identified by the
screening studies. Therefore, screening studies are based on composited samples analyzed
for a broad array of contaminants, and intensive studies are based on analysis of individual
128
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samples for only those analytes identified to be a potential problem. Analysis of individual
samples provides a measure of variation in the population thus allowing statistical testing
among locations and over time.
Should whole fish or fillets be analyzed?—The primary objective of most TVA fish
tissue studies is oriented toward human health. In that case, it makes little sense to examine
whole fish. Therefore, in most cases, TVA fish tissue studies are based on analysis of fillets.
Typically, analysis of whole fish is preferable when fish are used as "environmental monitors"
to determine the condition of the environment or to identify previously unknown
contaminants (FWGPM 1974 and McCracken 1983).
Should fillets have skin on or off? Should the bellvflap be left on the fillet?--The
decision point for both these questions is whether one wishes to produce a "worst-case," or a
less conservative, scenario. Fillets with skin and bellyflap left usually have higher
concentrations of most contaminants (worst-case), especially organochlorine contaminants,
than skin-off (best-case) fillets without the bellyflap. A study by Cornell University has
shown up to a 50 percent reduction in concentration of PCBs and mirex when comparing
"best-case" and "worst-case" prepared fillets (Gall and Voiland 1990). Based on the need
for a conservative approach in protection of public health, TVA studies are designed to
produce a worst-case estimate of contamination. This approach provides the best protection
to the fish consumer. All TVA analyses are conducted on fillets with bellyflap left on for all
species and skin left on for all species except catfish. Skin is removed from the catfish since
catfish skin is rarely, if ever, eaten with the fillet.
129
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Species Examined
The approach most commonly used in these studies is to examine a site as part of the
Reservoir or Stream Monitoring Fish Tissue Study (described in detail in Chapter 1), using
channel catfish as an indicator species. Channel catfish was selected as the indicator species
because it is highly sought by both commercial and sport fisherman, because individuals
usually have relatively high concentrations of most contaminants compared to other species,
and because a historical data base exists for that species.
If problems are identified, an intensive study is usually undertaken the next year that
would include analysis of individual channel catfish at a greater number of locations than
sampled in the screening study. Also, other important species would be examined at the
screening level. Depending upon their importance in the reservoir or stream and the
availability of funds, these species would include one or more of the following: largemouth
bass, striped bass, buffalo, crappie, carp, white bass, and possibly others. If problems are
identified in any of these species, they would be examined intensively (i.e., fillets analyzed
individually) during the subsequent year.
130
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PROCEDURES
Field Handling
Fish processing techniques have an influence on the accuracy and reliability of data derived
from tissue analysis. For this reason, consistency in the handling and processing of fish for
tissue analysis is vital.
Fish Collection
Fish can be collected by a variety of methods, for example, by various types of nets,
by electrofishing, or by commercial fishing gear. If fish come from commercial fisherman, a
biologist (TVA, state, or contractor) must accompany the fisherman and see that the fish
pulled are from an approved fishing/sampling area. Fish are removed from the gear, and the
appropriate number of each species, as specified in the workplan, are put in plastic bags (one
species per bag) in a cooler of ice. Dead fish may only be used if the gills are still red;
otherwise they are discarded. Fish cannot be held more than 24 hours in a cooler after
collection. No fish with flesh deteriorated beyond that desired for human consumption can
be included in the sample. Every reasonable effort is made to collect the desired number of
fish of each species as outlined in the workplan. Minimum length of black bass is 12 inches
for reservoir collections and 10 inches for stream collections. Channel catfish must weigh at
least one pound; striped bass/hybrids should be a minimum of two pounds, however, larger
fish are desired. If repeated attempts to collect large fish fail, smaller fish may be accepted.
The lab transfer sheet (attachment 1) originates with the person collecting the fish and
accompanies the sample until analyzed in the laboratory and/or archived. Each transfer of
131
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the sample from one location and/or person to another should be logged on the transfer sheet
with the signatures of the people delivering and receiving even if it is the same person.
Biological Lab Preparation
All work surfaces and cutting equipment used in fish processing should be washed
with soap, rinsed with tap water, followed by rinsing with pesticide grade propanol and
finally rinsing with distilled water. The cutting board is covered with heavy-duty aluminum
foil. Persons processing fish should wear sterile rubber gloves to prevent fish contamination.
At least two people are needed to process the fish, transcribe data and process fillets.
Data should be recorded using a No.2 pencil, or permanent pen and waterproof paper.
Much of the label can be completed prior to fish processing. The proper date for the record
sheet is that when the fish was collected, and not the date of processing. A sheet of clean
aluminum foil is used for wrapping each fillet, one sheet for the liver composite, and one
sheet to lay each fish on the scale while weighing.
Processing
Two waterproof labels (attachment 2) are completed for each fish (one for each
fillet). Total length and weight and the external observations, specified on the lab sheet
(attachment 3), are recorded for each fish. A mid-ventral cut is made from the vent
anteriorly with the scissors lifted to prevent damage to internal organs. The proportion of
the internal organs that are covered by fat after first opening the body cavity are noted, along
with the sex of the individual and complete observations of the internal organs as specified
132
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On the lab sheet. Any organs having abnormalities are removed and preserved in
formaldehyde for later study. After observations are recorded, the liver and then the gall
bladder are removed from the fish; care is taken not to rupture and contaminate the liver. If
the liver should be contaminated by the gall bladder it should be thoroughly rinsed with
distilled water. After the liver is weighed, it is discarded. Livers are not removed from carp
and smallmouth buffalo because of difficulty in removing livers from these fish without
contamination. Remaining viscera are then removed from the body cavity.
All scaled fish should have scales removed prior to opening the gut cavity; the skin is
left on. All catfish should have the skin removed with skinners or pliers (external cuts are
optional for skinning purposes). As little tissue as possible should be discarded with the skin.
Skin should also be removed from the belly section. When removing the fillets, start as close
to the head as possible and cut around the dorsal spine. Each fillet should be removed by a
mid-ventral cut that removes as much of the tissue as possible and includes the ribs and belly.
Any abnormalities present in the tissue of the fillet should be removed with as little of the
surrounding tissue as possible and preserved in formaldehyde for later study.
After both fillets are removed, the pelvic fin is cut out with scissors in a manner that
discards as little tissue as possible. Fat and entrails should be scraped off the inside of the
fillets with a knife. Fillets are rinsed in tap water followed by distilled water. Each fillet is
weighed and the fillet weight recorded on both the lab sheet and the label. Each fillet is
individually wrapped in the piece of foil on which it was weighed. If the fillet is very large, it
may be cut from the inside toward the outside, with a small amount near the skinned side
remaining in tact, and then folded on itself; foil should not be folded within the fillet. Each
133
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wrapped fillet and the label are placed individually in a plastic bag. As much air as possible
should be removed from the bag in order to conserve storage space. The above processing
procedures are repeated for all individuals of a species from each site.
After the electronic weight scales are tared, each subsequent liver should be added to
the aluminum foil containing the liver composite and weighed. If the workplan specifies
livers are to be archived, they are wrapped together in the aluminum foil, labeled, and placed
in a plastic bag then stored in a freezer.
Fillet Disposition
The two fillets from a fish will either be sent to the chemistry laboratory (one for
organic analysis and one for metals), or one will be sent to the chemistry laboratory for
appropriate analysis and the other archived. Random selection (coin toss) will decide which
fillet will be used for organics analysis and which for metals. If appropriate; a coin toss will
determine which fillet is sent to the laboratory for analysis and which one archived. This
information is indicated on the lab sheet.
All fillets from the same species from one site that will be used for organics will be
placed in a plastic bag with a common label that includes the following information: study,
river/reservoir, station or river mile, species, collection date and fish numbers with the side
(right or left) that will be used for this analysis. The label should also have "Organics" boldly
printed on it. The metals (or archived) fillets should be packaged the same way. The bag of
organics and the bag of metals will then be placed together in another plastic bag labeled
with the following information: study, reservoir/river, river mile, date, and species. All
134
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samples are to be placed in a freezer as soon as possible after processing. These same
procedures should be repeated for the next species and/or sampling location.
When more than one species is sampled from a site (intensive study), all species from
that site should be grouped together in another common bag for convenience later in finding
samples in the freezer. That bag should be labeled with the following information: study,
reservoir/river, river mile, species collected and their respective collection dates. If screening
studies include numerous sampling sites within a reservoir, these samples can be bagged
together and labeled appropriately.
All fillets slated for archival and ground tissue remaining from laboratory analyses are
stored frozen in Norris for approximately one year (until the following year's tissue samples
are ready to be stored). In special cases, tissue samples may be stored longer.
Chemical Laboratory Analyses
Laboratory Processing
Preparation of fillets for individual analysis is accomplished by homogenizing the
entire fillet. This is necessary because contaminants are not evenly distributed throughout
the fillet, and homogenization of only a portion would bias the results. Each fillet was
partially thawed and diced with a knife. Diced tissue was then thoroughly ground using a
mechanical grinder. After grinding, tissue was dispersed into glass jars and frozen pending
analysis.
A composite sample is prepared by taking an equal aliquot from each of five
independently homogenized fillets. Preparation of composite samples in this manner is
135
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necessary to avoid biasing results due to compositing fillets of different sizes. The
alternative way to avoid a size bias is to collect fish of a consistent size. This would allow
homogenizing all five fillets at the same time, thereby reducing time required for that step.
, However, TVA's experience has shown that this alternative is not desirable because it
increases collection costs, limits applicability of results to only the size of fish tested, and
prevents samples from maintaining their identity, if the need arises later for individual
analysis.
Analvtes
Fish collected for screening studies are usually analyzed for selected metals, PCBs,
and pesticides on EPA's Priority Pollutant List. Fish for intensive studies are analyzed only
for the contaminant of concern, which has been identified by screening studies or is known as
a historic problem. The most common contaminant of concern in the Tennessee Valley is
PCBs, with chlordane a distant second. Several TVA reservoirs have fish consumption
advisories due to PCB-contaminated fish.
The lipid content of a sample (determined gravimetrically and expressed as a
percentage) has been found to be an invaluable quality assurance tool, as well as being
essential in conducting spatial or temporal statistical analyses. For these reasons, lipid
content is determined on all samples.
PCBs are extracted with petroleum ether from homogenized fillets using a cell
disrupter. The extract is then cleaned with concentrated sulfuric acid and analyzed for
136
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Aroclors 1016, 1221, 1232, 1242, 1248, 1254, and 1260 using a precalibrated gas
chromatograph equipped with an electron capture detector and an electronic integrator.
Laboratory procedures for chlordane were provided in a previous report on fish from
Nickajack Reservoir in 1989 (Dycus 1990a) and will not be repeated here. Analyses for
pesticides are conducted using the 608 procedure.
Quality Assurance
TVA's standard Quality Assurance (QA) program requires running one replicate, one
spike, one blank, and one surrogate out of every ten samples. TVA also routinely splits
samples with other analytical laboratories if that agency is participating in fish tissue studies
on TVA waters.
Data Analyses
Screening Studies
Statistical analyses are not conducted on results from screening studies because
replicate samples are not collected. Results from these studies are compared to preselected,
tiered concentrations. If measured concentrations are low relative to the tiered
concentrations, then no follow-up studies are warranted. If measured concentrations are
high, follow-up studies would be conducted. More thorough explanation of this tiered
approach is provided in Chapter 1.
137
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Intensive Studies
A broad array of statistical techniques is used to further examine the results of the
laboratory analysis. A two-way analysis of variance (ANOVA) is used to compare lipid
content and/or fish size (length and weight) among sample locations or years.
Differences in PCB levels among locations and years are examined using either
ANOVA and Ryan-Einot-Gabriel-Welsch Multiple Range Test (REGW) or analysis of
covariance. Because PCBs are lipophilic compounds and have been found to accumulate
with fish size, these data are examined closely to determine if analysis of covariance is
needed to control PCB variability due to lipid content or fish size. The first step is to test the
null hypothesis that PCB levels do not depend upon lipid content or fish size for one or more
stations. This involves regressing PCB concentration against lipid content and fish size
simultaneously for each station. If the slopes for all stations are not different from zero
(failure to reject the null hypothesis), then no adjustment for lipid content is necessary and
ANOVA is the appropriate test. If the slopes differ from zero (rejection of null hypothesis),
covariance analysis is needed. Before proceeding to covariance analysis, data are tested for
homogeneity of slopes (parallel lines). If this null hypothesis is accepted, data are analyzed
using covariance analysis, comparing distances between the parallel regression lines.
Statistical analyses for chlordane concentrations are not reported due to interference
between PCB 1254 and cis-chlordane and interference between PCB 1260 and
trans-nanochlor. As a result, if PCB 1254 and/or 1260 are present, the appropriate
chlordane isomers would be reported as "interference" and no concentration provided. In
such cases the reported levels of chlordane would be conservative. This situation was
138
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recognized while analyzing the 1991 samples. Hence, chlordane concentrations for all
previous studies would over-estimate the true concentration.
Prior to statistical analyses, concentrations of PCBs are transformed to approximate a
normal distribution using a log]0 (x + 1) transformation (x + 1 is used because some values
are between zero and one). Lipid content is transformed using arc sine. An a of 0.05 is
chosen as the level of significance. Samples with less than detectable levels are included at
the detection limit in statistical analysis and developing averages.
139
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Attachment 1
FISH TISSUE SAMPLE LOG/TRANSFER FORM
Project,
Reservoir/River_
Location
Fish
Species Number
Collection E. Chen. Fillets • Fish Collection E. Chen. Fillets *
Date Number Left Right Liver Species Nuafcer Date Nunber Left Right Liver
* Indicate disposition of fillets and liver for analysis by placing the letter in the appropriate column. M = Metals 0 - Organics A = Archived
Date
Delivered by
(Signature)
Received by
(Signature)
Action
(e.g., N Lab to Chen Lab)
ABDQ966R
-------
Attachment 2
STUDY
f OIR
E MILE
SPECIES
SAMPLE NO. DATE / /
RIGHT FILLET ( ) LEFT FILLET ( ) LIVER ( )
TOTAL LENGTH iron
TOTAL WEIGHT grams
FILLET WEIGHT grams
STUDY.
RESERVOIR
RIVER MILE
SPECIES
SAMPLE NO. DATE / /
RIGHT FILLET ( ) LEFT FILLET ( ) LIVER ( )
TOTAL LENGTH mm
TOTAL WEIGHT grams
FILLET WEIGHT grams
STUDY
RESERVOIR
RIVER MILE
SPECIES
SAMPLE NO. DATE / /
R1 ILLET ( ) LEFT FILLET ( ) LIVER ( )
TC ENGTH mm
TOTAL WEIGHT grams
FILLET WEIGHT grams
STUDY
RESERVOIR
RIVER MILE
SPECIES
SAMPLE NO. DATE / /
RIGHT FILLET ( ) LEFT FILLET ( ) LIVER ( )
TOTAL LENGTH mm
TOTAL WEIGHT grams
FILLET WEIGHT grams
STUDY
RESERVOIR
RIVER MILE
SPECIES_
SAMPLE NO. DATE / /
RIGHT FILLET ( ) LEFT FILLET ( ) LIVER ( )
TOTAL LENGTH mm
TOTAL WEIGHT grams
FILLET WEIGHT grams
STUDY
RESERVOIR
RIVER MILE
SPECIES
SAMPLE NO. DATE / /
RIGHT FILLET ( ) LEFT FILLET ( ) LIVER ( )
TOTAL LENGTH mm
TOTAL WEIGHT grams
FILLET WEIGHT grams
-------
Project
River:
Reservoir :
Sta/Rlver Mile :
Attachment 3
Fish Tissue Studies - Biological Laboratory Form
Page
.of.
Sample Method :
Collectors ;
Processors :
Sample ID : Catfish
Gameflsh
Rough fish
Other
Fish Status :
Anesthetized
Near Dead
Dead
Other (frozen)
Sample
No.
Collect
Data
Spades
U
(mm)
Wt
(0m)
External
Observations
Internal
Observations
Left
Filet
wt (gm)
Right
Filet
wt fern)
Liver
wt (gm)
REMARKS
Eye
Oper.
Gill
Fin
Cond.
Fat
Uv.
Bile
Spl.
Kid.
Sex
Para
Coda
P84014
P39
P19
P85666
P85665
P85664
EWE
N-NORMAL
E (1 or 2 ) • EXOPTHALMIA
H (1 or 2) - HEMORRHAGIC
B (1 or 2; - BUND
M (1 Of 2) - MISSING
0T-OTHER
OPERCULUM
O- NO SHORTENING
1 •MILD
SHORTENING
2 - SEVERE
SHORTENING
QILL
N- NORMAL
F - FRAYED
C - CLUBBED
M - MARQINATE
OT - OTHER
EM
0-HEALED OR NO
EROSION
1 - MILD, ACTIVE
EROSION
2 - SEVERE. ACTIVE
EROSION
OQNDmON
N- NORMAL
R - ROBUST
8 - SKINNY
I - INFECTIONS
EAI
0-100*
USE 10%
INCREMENTS
TO IDENTIFY
PROPORTION
OF ORGANS
COVEF
BY FA]
LIVER
A-NORMAL
B-NODULES
OR UNUSUAL
GROWTHS
C-OTHER
BILE
0 - YELLOW, NOT FULL
1 - YELLOW, FULL
2 - LT. GREEN
3 - DK. GREEN
ffm
B - BLACK
R-RED
G- GRANULAR
NO-NODULES
E- ENLARGED
OT-THER
JODNEY
N-NORMAL
8 * SWOLLEN
G -GRANULAR
u-UROLrmtc
parasnrs
0-NONE
1 »FEW
2-NUMEROUS
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APPENDIX D
STATE OF TENNESSEE
LATEST FISH ADVISORY
143
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NEWS
Tennessee Department of Environment and Conservation
401 Cfturcn Street
Nashville. Tennessee
FOR MORE INFORMATION CONTACT:
Mary Locker: 615-532-0743
Paul Davis: 615-532-0625
FOR IMMEDIATE RELEASE
WEDNESDAY. MARCH 24.1993
NASHVILLE - The Department of Environment and Conservation's Division of Water Pollution
Control has announced that there will be no revisions at this time to the fishing advisories issued
in 1992.
The department issues fish consumption advisories when testing indicates that levels of
toxic materials in fish tissue exceed those considered to be protective of human health, "said
Water Pollution Control Director Paul Davis. "Since the consumption of contaminated fish
tissue is an avoidable risk, the department issues advisories so that citizens can make informed
choices concerning their health.
"The results of 1992 studies of sites where advisories already existed or areas where
additional studies were needed have not justified revising or removing existing advisories or
issuing new ones at this time,n Davis said. "However, the department will not hesitate to make
changes in the status of advisories during 1993 should new information become available."
Sites where samples were collected in 1992 include, but are not limited to. Wans Bar,
Chickamauga, Fort Loudoun, Douglas, Woods, Cheatham and Center Hill Reservoirs, as well as
the Mississippi, Wolf and Loosahatchie Rivers.
A list of the current advisories in Tennessee has been printed in the Tennessee Wildlife
Resources Agency's 1993 fishing regulations.
In order to assist citizens in their understanding of the stream posting process in
Tennessee, the Department of Environment and Conservation has prepared a free brochure
entitled "Tennessee Fishing Advisories." This publication explains the types of pollutants
impacting streams and the current locations of fishing advisories.
For more detailed information, or a copy of the brochure, contact the Department of
Environment and Conservation, Division of Water Pollution Control, 7th Floor, Life and
Casualty Annex, 401 Church Street, Nashville, Tennessee 37243-1534.
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FISHING ADVISORY BACKGROUND INFORMATION
There are two principal reasons for posting streams in Tennessee. The
first is when bacterial contamination poses a water contact threat. Sources of
bacteria are most frequently from inadequately treated discharges from
municipal sewage systems, but can also be from livestock holding areas and
urban runoff. This type of advisory warns the public to avoid coming in
contact with these waters through activities such as swimming, wading,
fishing and skiing.
Streams are also posted when average levels of toxic materials in the
edible portion of fish pose an increased cancer risk (or other serious Illness)
to the general public. The department uses information and guidance from
the U.S. Food and Drug Administration and the Environmental Protection
Agency on the various contaminants found in fish.
There are two levels of fish consumption advisories used in Tennessee.
The mildest form is a "limit consumption advisory," sometimes referred to as a
precautionary advisory. Scientific studies have shown that developing fetuses
and children may be more susceptible to the harmful effects of toxic matprialg
than are adults. Thus a precautionary advisory warns that children,
pregnant women and nursing mothers should not eat the type fish that is
contaminated. All others are warned to limit their consumption of these fish.
The second level of advisory is a do-not-consume warning. At t-hfc
level, all persons are advised to avoid eating the type fish contaminated.
The department makes every attempt to get advisory information to the
public. A press release is issued whenever a stream or lake is posted. The
department also places warning signs at significant public paints on
posted waters.
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CURRENT FISH TISSUE ADVISORIES (MARCH 1883)
STREAM COUNTY
Loosahatchie River Shelby
Wolf River
Mississippi River
McKellar Lake and
Nonconnah Croak
Boons Reservoir
North Fork
Holston River
Fort Loudoun
Reservoir
TeBico Lake
Pigeon River
Watts Bar
Reservoir
Melton Hill
Reservoir
East Fork of
Poplar Creek (tncl.
Poplar Creek
•rnPayment)
Nickajaek Reservoir
Shetey
Shelby
Sheby
Sullivan,
Washington
Sullivan,
Hawkins
Loudon,
Knox,
Blount
Loudon
Cocke
Roane,
Meigs,
Rhea
Roane
Knox,
Anderson
Anderson,
Roane
Hamilton,
Marion
PORTION
Mile 0.0-20 A
Mile 0.0-16.9
MS tin* to
mile 745
mile 0.0 to
Horn Lake Road
bridge (mili 1.8)
Entirety
Mile 0.0-6.2
TN/VAline
Entirety
(46 miles)
Entirety
(32.5 miles)
POLLUTANT TYPE ADVISORY
Chlordane Fish should not be consumed.
Chlordane Fish should not be consumed.
Chlordane Fish should not be consumed.
Commercial fishing ban.
Chbrdane Fish should not be consumed.
PCBs. chlordane Precautionary advisory for carp and catfish *
Mercury
PCBs
PCBs
N. Carolina line Dioxin
to Douglas Res.
Tennessee River PCBs
portion
Clinch River
arm
Entirety
Mile 0.0 ¦
15.0
Entirety
PCBs
PCBs
Mercury, metals,
org. chemicals
PCBs
Ftth should not be consumed.
Commercial fishing for catfish prohibited.
Catfish, large mouth bass over two pounds,
and iargemouth bass from the Little River
embayment should not be consumed.
Catfish should not be consumed.
Fsh should not be consumed.
Catfish, striped bass, and hybrid striped bass-
while bass (Cherokee bass) should not be eaten.
Precautionary advisory* for white bass, sauger,
carp, smallmouth buffalo and iargemouth baas.
Striped bass should not be consumed.
Precautionary advisory tor catfish and sauger.*
Catfish should not be consumed.
Fish should not be consumed.
Avoid contact with water.
Precautionary advisory tor catfish*.
Chattanooga Creek Hamilton GA line to mouth PCBs, chlordane Fish should not be consumed.
Woods Reservoir Franklin Entirety PCBs Catfish should not be consumed.
This list subject to revision.
* Precautionary Advisory - Children, pregnant women, and nursing mother* should not consume the fish species named.
All other persons should bmit consumption of the named species to 1.2 pounds per month.
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APPENDIX E
ALABAMA DEPARTMENT OF PUBLIC HEALTH
FISH CONSUMPTION ADVISORIES FOR THE
INDIAN CREEK EMBAYMENT (SPETEMBER 30, 1991)
ON WHEELER RESERVOIR AND SELECTED PORTIONS
OF WHEELER RESERVOIR (NOVEMBER 16, 1992)
147
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flLflBffllfi PUBLIC t-EALTH Orr ICE
NO.935 P002/0E3
OFFICE OF HEALTH MOMOTION AND WF0HVUT10N
STATE OWCEBUIUJWO. ROOM $87, UOWTQOMEAY, ALAWJM 881 KM 701
FOR IMMEDIATE RELEASE
CONTACT: Brian J. Hughes, Ph.D.
242-5131
Charies H. Woernle, M.D.
242-5131
The Alabama Department of Public Health announces the issuance of a fish
consumption advisory for the Indian Creek drainage area, including Huntsville Spring
Branch, near Triana. The department bases this decision on data indicating that
certain species of fish continue to exceed the Food and Drug Administration action
level of 5.0 parts per million of DDT in fish tissue. The species of fish with elevated
levels of DDT are channel catfish, smallmouth buffalo, brown bullhead, bigmouth
buffalo and white bass.
The Environmental Protection Agency banned the manufacture, sale and use of
DDT in 1972. However, a DDT manufacturing plant existed in this area between 1948
and 1970 with Olin Chemical Co. operating this facility under lease from Redstone
Arsenal for most of this period. Discharges from this plant contaminated Huntsville
Spring Branch and Indian Creek.
During the 1980s, Olin Chemical Co. developed and implemented remedial
action to protect humans and the environment from further DDT exposure. The
remedial action is a result of a consent decree which settled litigation between Oiln
and various plaintiffs Including the State of Alabama.
The data on DDT levels in fish tissue are a part of a long-term monitoring
program established pursuant to that consent decree.
Dr. Claude Earl Fox, state health officer, said, The DDT levels have declined
significantly in recent years due to the remediation of the contamination by industry,
and is expected to continue to decrease. In the eariy 1980s, before remediation
(more)
-------
,j:15 ALABftftt PUK-IC t-Eft_TH DrrlCE N2. S35 PaCo^U^
DOT advisory
Add one
began, the average concentration level among the above species ranged from 21 to
180 parte per million. In 1990 the range was from 3.1 to 41 parts per million.
"However, the levels remain high enouph that I remind fishermen to refrain from
eating these species of fish and other bottom-feeding species from this area. The
issuance of this advisory represents an effort to update the surrounding community
about the current situation."
DDT has been found to be a weak ca nogen in animal studies; however, no
evidence exists as to DDTs carcinogenic potential in man. Adverse effects on the liver
may occur but only at very high levels. A 1979 Centers for Disease Control study of the
residents of Triana revealed no DDT-related adverse health effects.
This advisory covers Indian Creek and Huntsvllle Spring Branch. The Alabama
Department of Public Health, Alabama Department of Environmental Management,
Alabama Department of Conservation and Natural Resources, and the Tennessee
Valley Authority will work together to collect additional data this fall on the Tennessee
River in the vicinity of Indian Creek. Results from these studies will be used to
determine If advisories for the Ten-essee River are appropriate.
-30-
9/23/91
-------
FOR IMMEDIATE RELEASE CONTACT: Brian J. Hughes, PhD.
Charies H. Woernle, MD.
242-5131
The Alabama Department of Public Health announces the expansion of an
existing fish consumption advisory for certain areas of the Tennessee River near
Triana, a small Madison County community.
The department bases this decision on fish sampling data from the Tennessee
Valley Authority indicating that certain species of fish exceed the Food and Drug
Administration tolerance level of 5.0 parts per million of DDT in fish tissue.
The information given to the Health Department by the TVA indicates elevated
levels of DDT in largemouth bass, channel catfish, and smalimouth buffalo one mile
either side of the area where Indian Creek and the Tennessee River join.
The public is advised not to eat these species from this area. Other bottom
feeding species (such as carp or sucker) in this area may also have high levels of DDT
in their tissues and should also be avoided.
Furthermore, elevated levels of DDT were found in channel catfish obtained in
the area where Indian Creek and the Tennessee River join downstream to the
interstate 65 bridge. The public is advised not to eat channel catfish from this extended
area.
The contamination resulted from the manufacturing of DDT in this area between
1948 and 1970. The DDT manufacturing plant near Redstone Arsenal discharged
DDT into the Huntsville Spring Branch and Indian Creek and may have also
contaminated fish in the Tennessee River.
Dr. Charies Woernle, state epidemiologist, said, "TVA agreed to obtain
additional information on DDT levels in fish tissue last year after meeting with the I]
and state health departments, and the Alabama Departments of Environmental
(more)
-------
DDT advisory
Add one
Management and Conservation and Natural Resources."
The DDT levels in fish tissue ranged from 5.0 to 43.3 parts per million in the
designated area among aii species of fish tested. Channel catfish further downstream
of the area ranged from 1.9 to 12.8 parts per million. A similar study will be conducted
this fall.
Dr. Woernie stated, "Many of the residents know about the previous advisory
issued last year regarding DDT contaminated fish tissue in the Huntsville Spring
Branch and Indian Creek area. Reductions in DDT levels in fish from this area have
been observed each year since cleanup and annual testing began in April 1986. The
issuance of a further advisory in this area represents an effort to keep people informed
about the current situation as new data develop."
The EPA banned the manufacture, sale and use of DDT in 1972. DDT has been
found to a weak cancer causing agent in animal studies; however, no evidence exists
as to DDTs cancer causing potential in man.
Adverse effects on the liver occur only at very high amounts. A former Centers
for Disease Control and Prevention study found no DDT-rsJated adverse health effects
in the residents of Triana.
Follow-up tests of fish in the expanded advisory area will be conducted this fall.
30-
11/16/92
-------
APPENDIX F
RESULTS OF A STUDY ON
MERCURY CONTAMINATION IN
LARGEMOUTH BASS FROM
TRIBUTARY RESERVOIRS
153
-------
Mercury Accumulation in Largemouth Bass
Initial fish tissue screening studies conducted by TVA found generally high concentrations
of mercury in channel catfish from tributary reservoirs compared to mainstream reservoirs.
Subsequent screening substantiated this observation. A more thorough examination of mercury
concentrations in fish from tributary reservoirs was conducted in autumn 1993 to futher define
and provide a database of mercury problems in tributary reservoirs. Largemouth bass were
collected from these reservoirs and analyzed for total mercury only. Handling and processing
procedures are described in Appendix C. Laboratory analyses were performed on composites of
five fish each. In an attempt to describe worse-case conditions, many largemouth bass weighing
over 1200 grams were also analyzed as individuals. All largemouth bass from Hiwassee Reservoir
were analyzed as individuals, as well as composites, to help evaluate fish size: mercury
concentration relationships.
The results of mercury analyses on largemouth bass are in Table F-l. Mercury
concentrations in largemouth bass composites were near or exceeded 0.5 (ig/g from six tributary
reservoirs.
Many of the large largemouth bass which were analyzed individually had relatively high
mercury concentrations, several approaching 1.0 |ig/g. Nine of 17 largemouth bass over 1200
grams had concentrations over 0.5 ng/g, the level to suggest further screening.
The relationship between total mercury concentration and total weight was examined with
regression analysis (Figure F-l). Generally, as weight increased, so did mercury concentration, as
evidenced by the regression line plotted in Figure F-l.
The relatively high concentrations of mercury in fish from many tributary reservoirs,
especially large fish, need further examination. Specifics of such a study had not been worked out
154
-------
at the time this report was prepared. Final study design will be developed by appropriate state
agencies and TV A.
155
-------
Table F-l Physical information and concentrations (ng/g) of total mercury in individual and
composited largemouth bass in the Tennessee Valley in 1993.
Hg
Collection Site
Species
Length (mm)
Weight (g)
Sex
LABID"
Individual
Bear Creek Reservoir
BCM 75
LMB
522
2265
FMALE
33444
0.91
BCM 75
LMB
475
1480
MALE
33295
BCM 75
LMB
409
990
FMALE
33295
BCM 75
LMB
401
925
FMALE
33295
BCM 75
LMB
395
855
FMALE
33295
BCM 75
LMB
33295
Little Bear Creek Reservoir
LBCRM 12
LMB
356
585
FMALE
33296
LBCRM 12
LMB
377
720
MALE
33296
LBCRM 12
LMB
382
810
FMALE
33296
LBCRM 12
LMB
562
2085
FMALE
33442
0.97
LBCRM 12
LMB
406
980
MALE
33296
LBCRM 12
LMB
33296
Hiwassee Reservoir
HIRM 77
LMB
395
848
FMALE
33411
0.40
HIRM 77
LMB
357
577
FMALE
33.413
0.21
HIRM 77
LMB
351
594
MALE
33416
0.5 0
HIRM 77
LMB
340
511
FMALE
33417
0.2 0
HIRM 77
LMB
33297
HIRM 85
LMB
380
874
FMALE
33418
0.40
HIRM 85-
LMB
370
732
FMALE
33419
0.40
HIRM 85
LMB
345
545
FMALE
33420
0.22
HIRM 85
LMB
344
589
MALE
33421
0.17
HIRM 85
LMB
433
1214
FMALE
33422
0.39
HIRM 85
LMB
33298
Chatuee Reservoir
HIRM 122
LMB
484
1255
FMALE
33423
0.45
HIRM 122
LMB
365
610
FMALE
33299
HIRM 122
LMB
424
839
FMALE
33299
HIRM 122
LMB
388
725
FMALE
33299
HIRM 122
LMB
355
482
FMALE
33299
HIRM 122
LMB
33299
Nottelv Reservoir
NOTRM24
LMB
547
2424
FMALE
33424
0.52
NOTRM24
LMB
453
1287
FMALE
33300
NOTRM 24
LMB
484
1619
FMALE
33300
NOTRM24
LMB
386
926
MALE
33300
NOTRM 24
LMB
359
546
MALE
33300
NOTRM 24
LMB
33300
Hg
Composite
0.71
0.6 0
0.33
0.30
0.23
0.44
156
-------
Collection Site
Hg Hg
Species Length (mm) Weight (g) Sex LABID* Individual Composite
Blue Ridge Reservoir
TOCCRM 54 LMB 360
TOCCRM 54 LMB 358
TOCCRM 54 LMB 323
TOCCRM 54 LMB 331
TOCCRM 54 LMB 417
TOCCRM 54 LMB
Norris Reservoir
CRM 80 LMB 416
CRM 80 LMB 332
CRM 80 LMB 470
CRM 80 LMB 395
CRM 80 LMB 365
CRM 80 LMB
CRM 125 LMB 418
CRM 125 LMB 385
CRM 125 LMB 387
CRM 125 LMB 397
CRM 125 LMB 376
CRM 125 LMB
PRM 30 LMB 353
PRM 30 LMB 387
PRM 30 LMB 441
PRM 30 LMB 401
PRM 30 LMB 403
PRM 30 LMB
Tellico Reservoir
LTRM 1.0 LMB 435
LTRM 1.0 LMB 409
LTRM 1.0 LMB 355
LTRM 1.0 LMB 357
LTRM 1.0 LMB 333
LTRM 1.0 LMB
LTRM 15 LMB 312
LTRM 15 LMB 442
LTRM 15 LMB 432
LTRM 15 LMB 325
LTRM 15 LMB 395
LTRM 15 LMB
MALE
33301
MALE
33301
r
33301
FMALE
33301
FMALE
33301
33301
MALE
33302
MALE
33302
FMALE
33451
MALE
33302
MALE
33302
33302
FMALE
33305
FMALE
33305
MALE
33305
FMALE
33305
MALE
33305
33305
FMALE
33307
FMALE
33307
FMALE
33307
FMALE
33307
FMALE
33307
33307
FMALE
33447
FMALE
33290
FMALE
33290
MALE
33290
FMALE
33290
33290
MALE
33292
FMALE
33292
FMALE
33448
MALE
33292
FMALE
33292
33292
668
578
491
520
912
932
468
1438
876
660
948
902
848
866
864
528
856
1106
828
956
1185
1042
694
540
478
428
1122
1280
402
898
157
-------
Hg Hg
Collection Site Species Length (mm) Weight (g) Sex LABID" Individual Composite
Fontana Reservoir
LTRM62
LMB
445
1352
FMALE
33449
LTRM62
LMB
374
858
MALE
33310
LTRM 62
LMB
350
814
MALE
33310
LTRM62
LMB
341
670
MALE
33310
LTRM 62
LMB
368
800
MALE
33310
LTRM 62
LMB
33310
LTRM 81
LMB
356
716
MALE
33311
LTRM 81
LMB
383
977
FMALE
33311
LTRM 81
LMB
340
637
MALE
33311
LTRM 81
LMB
347
539
FMALE
33311
LTRM 81
LMB
300
346
MALE .
33311
LTRM 81
LMB
33311
TUCKRM 3
LMB
549
2774
FMALE
33450
TTJCKRM 3
LMB
374
790
FMALE
33312
TUCKRM 3
LMB
353
584
FMALE
33312
TUCKRM3
LMB
309
434
FMALE
33312
TUCKRM 3
LMB
329
490
MALE
33312
TUCKRM 3
LMB
33312
Cherokee Reservoir
HRM 53
LMB
376
772
MALE
33313
HRM 53
LMB
378
812
FMALE
33313
HRM 53
LMB
372
670
MALE
33313
HRM 53
LMB
342
560
FMALE
33313
HRM 53
LMB
302
340
FMALE
33313
HRM 53
LMB
33313
HRM 75
LMB
424
1228
FMALE
33314
HRM 75
LMB
512
1972
FMALE
33428
HRM 75
LMB
388
920
MALE
33314
HRM 75
LMB
351
670
MALE
33314
HRM 75
LMB
337
556
FMALE
33314
HRM 75
LMB
33314
HRM 91
LMB
435
1194
FMALE
33430
HRM 91
LMB
414
1098
FMALE
33315
HRM 91
LMB
385
802
FMALE
33315
HRM 91
LMB
340
542
FMALE
33315
HRM 91
LMB
331
512
FMALE
33315
HRM 91
LMB
33315
Fort Patrick Henrv Reservoir
SFHRM9
LMB
489
2040
FMALE
33316
SFHRM 9
LMB
385
960
MALE
33433
SFHRM 9
LMB
401
1040
MALE
33316
SFHRM 9
LMB
373
858
MALE
33316
SFHRM 9
LMB
344
574
FMALE
33316
SFHRM 9
LMB
33316
158
-------
Hg
Hg
Collection Site
Species
Length (mm)
Weight (g)
Sex
LABID'
Individual
Composite
Boone Reservoir
SFHRM 19
LMB
421
1106
FMALE
33317
SFHRM 19
LMB
453
1362
FMALE
33434
0.26
SFHRM 19
LMB
435
1188
FMALE
33317
SFHRM 19
LMB
403
852
FMALE
33317
SFHRM 19
LMB
402
906
FMALE
33317
SFHRM 19
LMB
33317
0.14
SFHRM 27
LMB
463
1720
MALE
33435
0.50
SFHRM 27
LMB
474
1252
FMALE
33320
SFHRM 27
LMB
372
742
MALE
33320
SFHRM 27
LMB
379
740
MALE
33320
SFHRM 27
LMB
343
568
FMALE
33320
SFHRM 27
LMB
33320
0.22
WRM7
LMB
412
1046
FMALE
33322
WRM7
LMB
486
1636
FMALE
33436
0.51
WRM 7
LMB
392
922
MALE
33322
WRM 7
LMB
393
992
FMALE
33322
WRM7
LMB
336
566
MALE
33322
WRM7
LMB
33322
0.12
Wautaea Reservoir
WRM 37
LMB
495
2276
FMALE
33437
0.71
WRM 37
LMB
450
1418
FMALE
33325
WRM 37
LMB
420
1258
FMALE
33325
WRM 37
LMB
410
1068
FMALE
33325
WRM 37
LMB
392
988
FMALE
33325
WRM 37,
LMB
0.56
South Holston Reservoir
SFHRM 51
LMB
390
940
FMALE
33326
SFHRM 51
LMB
469
1572
FMALE
33438
0.60
SFHRM 51
LMB
447
1412
FMALE
33326
SFHRM 51
LMB
415
764
MALE
33326
SFHRM 51
LMB
397
758
MALE
33326
SFHRM 51
LMB
33326
0.45
a LAB ID = number assigned by TVA's Environmental Chemistry Laboratory. It is used to link laboratory
analysis data with physical data from fish.
b I = individual fish whose sex could not be determined.
159
-------
ON
o
Figure F-l Regression of mercury concentration vs total weight of largemouth
bass from tributary reservoirs in the Tennessee Valley in 1993.
1.2
J5JD
3!
a
C3
im
s
o
w
c
o
U
3
u
a
0.8
0.6
0.4
0.2
0
0
-
—
Linear Regression
¦ ¦
R-square = 0.54391
¦ m ^
b = 0.00029
a = 0.05657
¦
n = 31
;
¦
¦
-¦ ¦
¦
¦ ¦
-
¦
i
i , i
¦
i i i i i i i
500
1000 1500
Weight (grams)
2000
2500
3000
-------
Tennessee
Valley
Water Management
Chattanooga, Tennessee
May 1994
Authority
TENNESSEE VALLEY RESERVOIR AND STREAM QUALITY -1993
SUMMARY OF VITAL SIGNS AND USE SUITABILITY MONITORING
VOLUME I
CLEAN WATER
INITIATIVE
££££££££££££
-------
TENNESSEE VALLEY AUTHORITY
Resource Group
Water Management
TENNESSEE VALLEY RESERVOIR AND STREAM QUALITY - 1993
SUMMARY OF VITAL SIGNS AND
USE SUITABILITY MONITORING
Volume I
Report Coordinators:
Donald L. Dycus
and
Dennis L. Meinert
Authors and Contributors:
Steven A. Ahlstedt
Allen M. Brown
Neil C. Carriker
Tammy L. Carroll
Donald L. Dycus
Joe P. Fehring
Gary D. Hickman
Dennis L. Meinert
Charles F. Saylor
Damien J. Simbeck
Janis W. Strunk
Amy K. Wales
David H. Webb
Chattanooga, Tennessee
May 1994
-------
KEY CONTACTS FOR MONITORING FUNCTIONS
Monitoring Program Design
Neil Carriker
Don Dycus
(615) 751-7330
(615) 751-7322
Water Quality Monitoring
Physical/Chemical
Reservoirs
Streams
Bacteriological
Dennis Meinert
Jan Strunk
Joe Fehring
(615) 751-8962
(615) 751-8637
(615) 751-7308
Sediment Quality
Physical/Chemical
Toxicity
Dennis Meinert
Damien Simbeck
(615) 751-8962
(205) 729-4549
Biological Monitoring
Fish
Ecology
Reservoirs
Streams
Consumption
Benthic Macroinvertebrates
Reservoirs
Streams
Ecological Health
Gary Hickman
Charlie Saylor
Don Dycus
Amy Wales
Steve Ahlstedt
Don Dycus
Dennis Meinert
(615) 632-1791
(615) 632-1779
(615) 751-7322
(615) 751-7831
(615) 632-1781
(615) 751-7322
(615) 751-8962
ii
-------
CONTENTS - VOLUME I
TABLES vi
FIGURES vi
EXECUTIVE SUMMARY ix
1.0 INTRODUCTION 1
1.1 Background 1
1.2 Objectives 1
1.3 Summary Report Description 2
2.0 DATA COLLECTION METHODS 5
2.1 Vital Signs Monitoring 5
2.1.1 Introduction 5
2.1.2 Reservoir Vital Signs Monitoring 7
Physical/Chemical Characteristics of Water 7
Acute Toxicity and Physical/Chemical Characteristics of Sediment 8
Benthic Macroinvertebrate Community Sampling 9
Fish Assemblage Sampling 10
Aquatic Macrophytes 11
2.1.3 Stream Vital Signs Monitoring 11
Physical/Chemical Characteristics of Water 12
Acute Toxicity and Physical/Chemical Characteristics of Sediment 13
Benthic Macroinvertebrate Community Sampling 13
Fish Community Sampling 14
2.2 Use Suitability Monitoring 14
2.2.1 Bacteriological Sampling 15
2.2.2 Fish Tissue Sampling 15
3.0 ECOLOGICAL HEALTH AND USE SUITABILITY DETERMINATION METHODS 29
3.1 Vital Signs Monitoring 29
3.1.1 Introduction 29
3.1.2 Reservoir Ecological Health 29
Dissolved Oxygen (DO) Rating Scheme 30
Chlorophyll Rating Scheme 32
Sediment Quality Rating Scheme 33
Benthic Community Rating Scheme 34
Fish Assemblage Rating Scheme 36
Overall Reservoir Health Determination 38
3.1.3 Stream Ecological Health 40
Nutrient Concentration Rating Scheme 41
Sediment Quality Rating Scheme 41
Benthic Community Rating Scheme 42
Fish Community 43
3.2 Use Suitability 44
3.2.1 Bacteriological Quality Evaluation 44
3.2.2 Fish Tissue Consumption Advisories 45
iii
-------
4.0 HYDROLOGIC OVERVIEW OF 1993 59
4.1 Atmospheric Temperature 61
4.2 Rainfall 62
4.3 Streamflow 63
5.0 DISCUSSION 67
5.1 Vital Signs Monitoring 69
5.1.1 Reservoirs 69
Run-Of-The-River Reservoirs 69
Tributary Reservoirs 71
5.1.2 Streams 74
5.2 Use Suitability Monitoring 75
5.2.1 Bacteriological Studies 75
5.2.2 Fish Tissue Studies 76
Screening Studies 76
Intensive Studies 77
WATERSHED-BY-WATERSHED SUMMARY
6.0 KENTUCKY RESERVOIR WATERSHED 81
6.1 Kentucky Reservoir 83
6.2 Beech Reservoir 85
7.0 DUCK RIVER WATERSHED 87
7.1 Normandy Reservoir 89
7.2 Duck River Stream Monitoring Site 91
8.0 PICKWICK RESERVOIR - WILSON RESERVOIR WATERSHED 93
8.1 Pickwick Reservoir 95
8.2 Wilson Reservoir 97
8.3 Bear Creek Reservoir 99
8.4 Little Bear Creek Reservoir 101
8.5 Cedar Creek Reservoir 103
8.6 Bear Creek Stream Monitoring Site 105
9.0 WHEELER RESERVOIR - ELK RIVER WATERSHED 107
9.1 Wheeler Reservoir 109
9.2 Tims Ford Reservoir Ill
9.3 Elk River Stream Monitoring Site 113
10.0 GUNTERSVILLE RESERVOIR - SEQUATCHIE RIVER WATERSHED 115
10.1 Guntersville Reservoir 117
10.2 Sequatchie River Stream Monitoring Site 119
11.0 NICKAJACK RESERVOIR - CHICKAMAUGA RESERVOIR WATERSHED 121
11.1 Nickajack Reservoir 123
11.2 Chickamauga Reservoir 125
iv
-------
12.0 HIWASSEE RIVER WATERSHED 127
12.1 Hiwassee Reservoir 129
12.2 Chatuge Reservoir 131
12.3 Nottely Reservoir 133
12.4 Blue Ridge Reservoir 135
12.5 Ocoee Reservoir No. 1 (Parksville Reservoir) 137
12.6 Hiwassee River Stream Monitoring Site 139
13.0 WATTS BAR RESERVOIR, FORT LOUDOUN RESERVOIR,
AND MELTON HILL RESERVOIR WATERSHED 141
13.1 Watts Bar Reservoir 143
13.2 Fort Loudoun Reservoir 145
13.3 Melton Hill Reservoir 149
13.4 Emory River Stream Monitoring Site 151
14.0 CLINCH RIVER AND POWELL RIVER WATERSHED 153
14.1 Norris Reservoir 155
14.2 Clinch River Stream Monitoring Site 157
14.3 Powell River Stream Monitoring Site 159
15.0 LITTLE TENNESSEE RIVER WATERSHED 161
15.1 Tellico Reservoir 163
15.2 Fontana Reservoir 165
15.3 Little Tennessee River Stream Monitoring Site 167
16.0 FRENCH BROAD RIVER WATERSHED 169
16.1 Douglas Reservoir 171
16.2 French Broad River Stream Monitoring Site 173
16.3 Nolichucky River Stream Monitoring Site 175
17.0 HOLSTON RIVER WATERSHED 177
17.1 Cherokee Reservoir 179
17.2 Fort Patrick Henry Reservoir 181
17.3 Boone Reservoir * 183
17.4 South Holston Reservoir 185
17.5 Watauga Reservoir 187
17.6 Holston River Stream Monitoring Site 189
REFERENCES 191
CONTENTS FOR VOLUME II 197
v
-------
TABLES
2.1 Run-of-the-River Reservoirs-Basic Monitoring Strategy 20
2.2 Stream Vital Signs Monitoring Locations, 1993 25
2.3 Physical/Chemical Measurements - Sediment 26
3.1 Reservoir Benthic Macroinvertebrate Community Metrics
and Scoring Criteria Developed for Tennessee Valley Reservoirs 47
3.2 Core Fish Species List With Trophic Tolerance and
Reproductive Designations for Use in RFAI for TVA Reservoirs, 1993 48
3.3 Reservoir Fish Assemblage Index Metrics and Scoring Criteria
Developed for TVA Run-of-the-River Reservoirs 50
3.4 Benthic Macroinvertebrate Community Index of Biotic Integrity Metrics and
Scoring Criteria Developed for Tennessee Valley Streams 52
3.5 Fish Community Index of Biotic Integrity Metrics and Scoring Criteria
Developed for Tennessee Valley Streams 53
3.6 Computational Method for Evaluation of Reservoir Health
Wilson Reservoir - 1993 (Run-of-the-River Reservoir) 56
3.7 Computational Method for Evaluation of Reservoir Health
Cherokee Reservoir - 1993 (Tributary Storage Reservoir) 57
4.1 Characteristics of Vital Signs Reservoirs 66
FIGURES
2.1 Schematic of Key Reservoir Sampling Areas 17
2.2 Reservoir Vital Signs Monitoring Locations - 1993 18
2.3 Stream Vital Signs Monitoring Locations - 1993 19
3.1 Cross-Section of Tellico Reservoir Forebay Showing Areas
Where Summer DO Concentrations Averaged Less than or Equal to 2 mg/L 46
4.1 Temperature, Precipitation, and Runoff - Tennessee River Basin, 1993 64
4.2 Average Annual Tennessee River Flows Showing Contributions of
Major Tributaries and Local Inflows 65
vi
-------
FIGURES
(Continued)
5.1 Overall Ecological Health of Run-of-the-River Reservoirs
in the Tennessee Valley in 1993 79
5.2 Overall Ecological Health of Tributary Reservoirs
in the Tennessee Valley in 1993 80
6.1 Map of Kentucky Reservoir Watershed Showing
Reservoir Monitoring Sites in 1993 82
7.1 Map of the Duck River Watershed Showing.
Stream and Reservoir Monitoring Sites in 1993 88
8.1 Map of the Pickwick Reservoir - Wilson Reservoir Watershed Showing
Stream and Reservoir Monitoring Sites in 1993 94
9.1 Map of Wheeler Reservoir - Elk River Watershed Showing
Stream and Reservoir Monitoring Sites in 1993 108
10.1 Map of the Guntersville Reservoir - Sequatchie River Watershed
Showing Stream and Reservoir Monitoring Sites in 1993 116
11.1 Map of the Nickajack Reservoir - Chickamauga Reservoir Watershed
Showing Reservoir Monitoring Sites in 1993 122
12.1 Map of the Hiwassee River Watershed
Showing Stream and Reservoir Monitoring Sites in 1993 128
13.1 Map of the Watts Bar Reservoir, Fort Loudoun Reservoir, and Melton Hill Reservoir
Watershed Showing Stream and Reservoir Monitoring Sites in 1993 142
14.1 Map of the Clinch River and Powell River Watershed Showing
Stream and Reservoir Monitoring Sites in 1993 154
15.1 Map of the Little Tennessee River Watershed Showing
Stream and Reservoir Monitoring Sites in 1993 162
16.1 Map of the French Broad River Watershed Showing
Stream and Reservoir Monitoring Sites in 1993 170
17.1 Map of the Holston River Watershed Showing
Stream and Reservoir Monitoring Sites in 1993 178
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EXECUTIVE SUMMARY
TVA initiated a systematic, Valley-wide water quality and aquatic ecological monitoring
program in 1986. The program started with a stream component, and a reservoir monitoring
component was added in 1990. The two primary objectives of these monitoring efforts are to
evaluate the ecological health (Vital Signs Monitoring) of major streams and reservoirs in the
Tennessee Valley and to examine how well these water resources meet the swimmable and fishable
goals of the Clean Water Act (Use Suitability Monitoring).
Vital Signs Monitoring
Stream monitoring has been conducted on 12 large tributaries since 1986. Beginning in 1994,
six additional tributaries will be monitored; all with watersheds of at least 500 square miles.
Reservoir monitoring started with 12 reservoirs (mostly mainstream reservoirs) in 1990 and has
expanded progressively to the full complement of 30 reservoirs in 1993. No further expansion of
either stream or reservoir monitoring is planned. This report summarizes results of these monitoring
efforts in 1993. Volume I is the main body of the report and Volume II is a data summary organized
by sample locations within watershed areas.
Until 1991, the ecological health evaluations were based on subjective evaluation of the data.
A weight-of-evidence approach was used-a stream or reservoir was deemed healthy if most of the
physical, chemical, and biological monitoring components appeared healthy. Beginning with the 1991
results, a more quantitative approach was developed that has been used the last three years. This
approach integrates information on important indicators of ecological health. For reservoirs, five
indicators are used-dissolved oxygen, chlorophyll, sediment quality, benthic macroinvertebrates, and
fishes. Stream evaluations are similar except dissolved oxygen is not rated and nutrient
concentrations are substituted for chlorophyll concentrations. For each indicator (or metric), scoring
criteria are developed that assign a score ranging from 1 to 5 representing very poor to excellent
conditions, respectively. Scores for all indicators at a location are summed. For streams and smaller
reservoirs, only one site is monitored. For larger reservoirs, multiple sites are monitored, and the
overall reservoir score is achieved by totaling scores for all locations. The resulting total is divided
by the maximum possible score. Thus, the possible range of scores is from 20 percent (all metrics
very poor) to 100 percent (all metrics excellent). Hence, an overall ecological health rating of good,
fair, or poor is obtained for each stream site or reservoir. A health rating border-line between two of
these categories is considered poor-fair or fair-good. Each year, the most recent information is
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evaluated with the same basic approach, modified to incorporate improvements based on comments
from reviewers and additional data.
Stream monitoring results for 1993 indicated seven streams rated good (three of these received
perfect scores), three streams rated fair to good, and one stream rated poor. Full evaluation was not
possible for one stream because only three of the four indicators were monitored in 1993. The only
stream to receive a poor rating was the French Broad River. This overall rating was caused by poor
scores for nutrients and fishes, a fair score for benthos, and a good score for sediment quality.
Reservoirs are stratified into two groups for evaluation: run-of-river reservoirs and deep
storage reservoirs. Separate scoring criteria were used for the two categories. Overall ratings for the
11 run-of-river reservoirs in 1993 ranged from 58 to 88 percent. Four reservoirs rated good (75 to
88 percent), three rated fair to good (71 to 73 percent), three rated fair (63 to 68 percent), and one
rated poor to fair (58 percent). Overall ratings for the 19 storage reservoirs ranged from 52 to 72
percent. Two reservoirs rated fair to good (both 72 percent), 14 rated fair (58 to 67 percent), and
three rated poor (52 to 56 percent).
Most streams and reservoirs had ratings comparable to those observed in 1991 and 1992.
Tributary reservoirs had generally poorer ratings, primarily because of low dissolved oxygen in the
hypolimnion. This is an ecologically undesirable condition that is partly due to the strong thermal
stratification that occurs in deep reservoirs with relatively long retention times.
Use Suitability Monitoring
Use Suitability Monitoring provides screening level information on the suitability of selected
areas within TV A reservoirs for water contact activities (swimmable) as determined by bacteriological
studies and suitability of fish from TVA reservoirs for human consumption (fishable) as determined
by fish tissue studies.
Bacteriological Studies—Bacteriological samples are collected at over 260 sites in the
Tennessee Valley. These include designated swimming areas, canoe access sites, highly used
recreational areas, and selected nonrecreation sites that provide information on pollution sources or
inflow stream water quality. Recreation sites are sampled at least once every two years.
In 1993, 71 swimming areas and 14 canoe access points were sampled for bacteriological
conditions. All but two swimming areas met the regulatory criterion to be considered safe. Even
those two sites met the criterion if samples collected after heavy rains were excluded. Four canoe
access points on the Duck River exceeded the criterion, both in dry and wet weather.
Bacteriological sampling at nonrecreational areas was conducted at 35 sites in 1993. Only one
reservoir site and two stream sites failed to meet recreation criteria.
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These results are consistent with previous surveys. Fecal coliform concentrations were
generally lower in 1993 due to lower than normal summer rainfall. Bacteriological water quality in
most areas of TV A reservoirs is good. In streams it is much poorer, especially after rainfall.
Fish Tissue Studies-Fish tissue studies examine fillets from important fish species for selected
metals, pesticides, and polychlorinated biphenyls (PCBs) on the U.S. Environmental Protection
Agency's list of priority pollutants. Resulting data are provided to appropriate state agencies to
determine whether further study is needed or fish consumption advisories should be issued. Fish
tissue data reported here represent autumn 1992 collections. Results for fish collected in autumn
1993 were not available at the time this report was prepared due to the time delay required for
laboratory analysis.
Results of fish tissue screening studies in 1992 did not reveal any new areas in need of
intensive investigations. Concentrations of at least one contaminant were high enough to warrant
sampling again at the screening level in 1993. Results of intensive studies (i.e., in-depth studies on
waterbodies where there are known or suspected problems) did not indicate substantial changes from
previous years.
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1.0 INTRODUCTION
1.1 Background
The Tennessee Valley Authority (TVA) started a Stream Monitoring Program in 1986 to
evaluate the major tributaries of the Tennessee Valley at fixed locations. A parallel program,
Reservoir Monitoring, was begun in 1990 when funds were appropriated by Congress for TVA to
strengthen its stewardship responsibilities. The combined Stream and Reservoir Monitoring efforts
consolidated several newly-developed activities along with several existing activities to form an
integrated program. These monitoring efforts, in addition to River Action Team watershed
examinations and public information/educational activities, are now part of TVA's comprehensive
Clean Water Initiative.
1.2 Objectives
Objectives of these monitoring efforts are to provide information on the "health" or
integrity of the aquatic ecosystem in major Tennessee River tributaries and reservoirs and to provide
screening level information for describing how well these water resources meet the "fishable" and
"swimmable" goals of the Clean Water Act.
The ecological integrity of stream and reservoir ecosystems is examined as part of an
activity called Vital Signs monitoring. The basis of Vital Signs monitoring is examination of key
physical, chemical, and biological indicators to evaluate the health of each stream or reservoir and to
target detailed assessment studies if significant problems are found. In addition, this information
establishes a baseline for comparing future water quality conditions as watershed improvements are
made.
Another activity, Use Suitability monitoring, examines how well streams and reservoirs
meet the fishable and swimmable goals of the Clean Water Act. Examination of levels of toxic
contaminants in fillets from important fish species is the basis for the fishable use evaluation.
Swimmable or water contact uses are examined by conducting bacteriological sampling at designated
swimming beaches and other highly used recreation areas.
Using a quantitative approach to evaluate ecological health of water resources is relatively
new, especially for reservoirs. This is only the third year TVA has used this approach, and we
continue to make improvements based on experience gained each year. Ecological health evaluations
drawn from this newly implemented monitoring program are subject to revision in future
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years as more data and experience are acquired on each reservoir. We welcome comments and
suggestions for improvements in these ecological health evaluation methodologies. Please send
comments/suggestions to the address above or contact appropriate individuals listed under key
contacts on page ii.
1.3 Summary Report Description
Volume I of this report summarizes and integrates results from TVA's stream and
reservoir monitoring activities in 1993. Chapter 1 provides background and objectives for the
monitoring program. Chapter 2 describes the basis for study design and specific methods for sample
collection. Chapter 3 describes the philosophical approach and data evaluation methods used for each
indicator to determine stream and reservoir ecological health.
Chapter 4 provides an overview of hydrologic and meteorologic conditions for 1993.
Conditions in streams and reservoirs are greatly affected by streamflow, rainfall, and temperature, as
well as by physical and geologic characteristics of the watershed. Dams, and resulting reservoirs'
dynamics, are important factors in the ecological health of regulated river systems. It is important to
consider all these variables and their effects in evaluating ecological conditions of the Tennessee River
system in any given year.
Chapter 5 discusses the 1993 monitoring results from a Valley-wide perspective.
Discussion topics include an overview of ecological conditions, ecological indicators which "drove"
the health ratings, changes from previous years, embayment monitoring (initiated in 1993), and
swimmable and fishable conditions.
Chapters 6-17 provide a watershed-by-watershed summary and conclusions for each of the
12 watershed drainage areas in the Tennessee Valley. Each chapter provides a physical description of
the watershed followed by a description of the physical characteristics, ecological health, and use
suitability of each reservoir and stream monitoring site within the watershed. The ecological health
evaluation is based on an integration of physical, chemical, and biological information gathered using
the different Vital Signs monitoring tools.
Detailed summaries of 1993 results on each reservoir and stream are provided in Volume
II of this report. Volume II is for technical audiences who prefer to form their own evaluation of
conditions. It also serves as a detailed technical summary of conditions at TV A monitoring sites in
1993.
In addition to this technical summary report, a nontechnical document, RiverPulse,is
available. RiverPulse (TVA, 1994) is broadly distributed to Tennessee Valley residents and users of
TVA reservoirs. Annual issues of the technical report have been prepared since 1990, and annual
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issues of Riverpulse are available for 1991, 1992, and 1993. There also is a series of annual activity
reports providing detailed results for each monitoring tool (e.g., water, sediment, benthos, fish, etc.).
These detailed reports provide the basis for the summary report. Specific citations for summary and
detailed reports are in the list of references. Copies of any of these documents are available from:
TV A Water Management Library, 1101 Market Street, HB 2C-C, Chattanooga, TN 37402,
Telephone: (615) 751-7338, FAX: (615) 751-7479.
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2.0 DATA COLLECTION METHODS
2.1 Vital Signs Monitoring
2.1.1 Introduction
The study design for Vital Signs Monitoring is based on meeting the objectives outlined in
Section 1.2. Several assumptions are fundamental to the study design:
1. Ecological health evaluations must be based on information on physical, chemical, and
biological components of the ecosystem;
2. Vital Signs monitoring is a long-term effort to document the status of the
river/reservoir system and track results of water quality improvement efforts;
3. Monitoring methods must be responsive by providing current information to resource
managers;
4. The basic design must be considered dynamic and flexible, rather than rigid and static,
and must allow adoption of new environmental monitoring techniques as they develop
to meet specific needs; and
5. This is a monitoring program; it does not address specific cause/effect mechanisms.
(The step beyond monitoring is assessment in which cause/effect investigations would
target specific, identified concerns.)
Three important aspects were considered in establishing the study design: representative
sampling locations; important ecological indicators; and frequency of sampling. The program that
emerged balances these considerations as follows.
Sampling Locations-For reservoirs, the following three areas were selected for
monitoring: the inflow area, generally riverine in nature; the transition zone or mid-
reservoir area where water velocity decreases due to increased cross-sectional area,
suspended materials begin to settle, and algal productivity increases due to increased water
clarity; and the forebav. the lacustrine area near the dam, Figure 2.1. Overbanks,
basically the floodplain which was inundated when the dam was built, were included in
transition zone and forebay areas. Another important reservoir area, embayments, also
was considered. However, monitoring all embayments is beyond the scope of this
program. Previous studies have shown that ecosystem interactions within an embayment
are mostly controlled by activities and characteristics within the embayment watershed,
usually with relatively little influence from the main body of the reservoir. As a result,
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only four, large embayments, all with drainage areas greater than 500 square miles and
surface areas greater than 4500 acres, are included in the Vital Signs Monitoring Program.
These were added in 1993 and are reported on here for the first time.
The stream monitoring sampling locations were located to sample the cumulative water
quality for as large a percentage of a tributary watershed as possible, with sampling
locations located in the free-flowing reaches of the river near the downstream end of the
watershed, but upstream of any impounded water.
Ecological Indicators-Selection of appropriate ecological indicators for monitoring
was tailored to the specific objective and type of monitoring location. Physical, chemical,
and biological indicators were selected to provide information from various habitats or
ecological compartments on the health of that particular habitat or compartment. In
reservoirs (Figure 2.1) the open water or pelagic area was represented by physical and
chemical characteristics of water (including chlorophyll) in midchannel. The shoreline or
littoral area was evaluated by sampling the fish community. The bottom or benthic
compartment was evaluated using two indicators: quality of surface sediments in
midchannel (determined by chemical analysis of sediments and acute toxicity testing of
pore water); and examination of benthic macroinvertebrates from a transect across the full
width of the sample area (including overbanks if present).
In streams, all available habitats were included to truly characterize the sample site.
This is more easily accomplished in streams than in reservoirs because most habitats are
visible. The same basic indicators used for reservoirs were also used in streams.
For both reservoirs and streams, information from each indicator was evaluated
separately and results were then combined (without weighing) to arrive at an overall
evaluation of reservoir ecological health. (See Chapter 3 for more details on the ecological
health evaluation and scoring process.)
Sampling Frequency-Sampling frequencies were selected to take into consideration
the expected temporal variation for each indicator. Physical and chemical components
vary significantly in the short term, whereas biological components are more representative
of long-term conditions. As a result, sampling for physical and chemical indicators is
needed more frequently than biological indicators. In reservoirs, physical and chemical
indicators were examined monthly from spring to fall and in streams every other month
throughout the year. Biological indicators were sampled once each year for reservoir and
stream sites. In reservoirs, benthic macroinvertebrate sampling was conducted in early
spring (February-April), and fish assemblage sampling was conducted in autumn
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(September-November). In streams, benthic and fish community sampling is conducted in
late spring-early summer (May-June).
2.1.2 Reservoir Vital Signs Monitoring
The Vital Signs component of reservoir monitoring includes four main activities to
examine and evaluate reservoir health:
(1) physical/chemical characteristics of water;
(2) acute toxicity and physical/chemical characteristics of sediment;
(3) benthic macroinvertebrate community sampling; and,
(4) fish assemblage sampling.
(In addition, aquatic macrophyte community information is included
to provide a more comprehensive evaluation of each reservoir's ecological health.)
Data collection methods for each of these activities are given below. Sampling locations
and specific monitoring activities for each reservoir are listed in Table 2.1 and shown in Figure 2.2.
Physical/Chemical Characteristics of Water-In 1993, physical/chemical water quality
variables were measured at a total of 57 sampling locations on 30 reservoirs. Three specific QA/QC
measures were incorporated in the reservoir physical/chemical water sampling activities. These
included: (1) collection and analysis of triplicate sets of water samples once during the year at all
forebay sampling locations to assess sample collection, laboratory analysis, and natural sample
variability; (2) preparation and analysis of sample container blanks each collection day to assess the
degree of contamination associated with the sample bottles and/or the sample handling processes; and,
(3) preparation and analysis of sample filtration blanks with each set of filtered samples to assess the
degree of contamination associated with the field sample filtration and handling.
The water quality monitoring activities on the Vital Signs reservoirs followed a "basic"
(11 run-of-the-river reservoirs) or a "limited" (19 tributary reservoirs) sampling strategy (Table 2.1).
Baric-Monitoring on the run-of-the-river reservoirs included monthly water
quality surveys (April through September) at forebays and transition zones. Basic
monthly water quality sampling included in situ water column measurements of
temperature, dissolved oxygen, pH, and conductivity; Secchi depth measurements;
surface fecal coliform; photic zone (defined as twice the Secchi depth) composite
chlorophyll-a samples; and photic zone composite and near-bottom samples for
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nutrients (organic nitrogen, ammonia nitrogen, nitrate+nitrite nitrogen, total
phosphorus, and dissolved orthophosphorus), total organic carbon, color, and
suspended solids. Physical/chemical water quality sampling was not conducted at
most run-of-the-river reservoir inflows because most of these locations are
tailwater areas of upstream dams; water quality characteristics there are more
representative of processes in the upstream reservoir.
Limited-Tributary storage reservoirs were sampled monthly (April through
October) for a smaller list of parameters. The approach was the same as for the
run-of-the-river reservoirs, except that no fecal coliform, color, or suspended
solids samples were collected, and only photic zone composites for nutrients and
organic carbon samples were collected and only in April and August. The April
and August nutrient samplings were designed to provide information on nutrient
concentrations available at the beginning of the growing season, then near the end
of the growing season. Forebays were sampled on all these reservoirs, and mid-
reservoir locations were sampled on all but the smaller reservoirs.
Physical/chemical water quality data were stored on EPA's water quality data storage and
retrieval (STORET) system. Reservoir health evaluation methods used to assess physical/chemical
quality are described below (Section 3.1.2).
Acute Toxicity and Phvsical/Chemical Characteristics of Sediment—Annual sediment
samples and near-bottom water samples were collected during the summer of 1993 from 59 locations,
i.e., the forebays and transition zones (or mid-reservoir) of the 11 mainstream reservoirs and 19
tributary reservoirs as shown in Table 2.1. In addition, ten of the 59 locations were randomly
selected for replicate QA/QC sampling. Sampling efforts were repeated at each of the ten sites.
Replicate samples were handled and processed independently. Results from these ten sets of
replicates were used to assess field methods consistency, variations in laboratory toxicity and
physical /chemical analyses, and spatial homogeneity of the sediment. Eckman dredge samplers were
used to collect the top three centimeters of sediment and Kemmerer or Isco water samplers were used
to collect the near-bottom water. Each sediment sample was a composite of at least three subsamples
independently collected at each sampling location from the original stream channel bed. At each
sampling site, the subsamples were composited, thoroughly mixed to uniform color and consistency,
and split into two fractions: one fraction for acute toxicity testing, and one fraction for
physical/chemical analyses. Samples were placed on ice immediately after collection, compositing,
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and splitting, and were shipped or carried to the appropriate laboratory. One split from each
sampling location and the sample of near-bottom water were shipped to the Toxicity Testing
Laboratory (TTL) for toxicity testing; the other split at each sampling location was shipped or carried
to the Environmental Chemistry Laboratory (ECHE) for chemical and physical analyses.
Acute Toxicity Testing-Within 36 hours of collection, all sediment samples
were screened for toxicity using Rotox® (rotifer, Brachionus calvciflorus survival)
and daphnid (Ceriodaphnia dubia) acute tests. Organisms were exposed to
undiluted interstitial (pore) water from the sediment and near bottom water.
Interstitial water was obtained by refrigerated centrifugation of sediment. Control
water consisted of Moderately Hard Reconstituted Water, MHRW (TVA, 1992b),
(hardness of 80-100 mg/L as CaC03) enriched with 10 percent Tennessee River
water from TTL's experimental channels for the daphnid test and MHRW adjusted
to pH=7.5 using HC1 for the rotifer test. All samples were aerated to bring
dissolved oxygen levels to near saturation (8.4 mg/L at 25°C) before testing.
Water chemistry (temperature, DO, pH, conductivity, alkalinity, and hardness) was
measured for all samples and controls. After centrifugation of the sediment, pore
water samples were collected and preserved and sent to the Environmental
Chemistry Laboratory for un-ionized ammonia analysis. Four replicates of five
individuals each were used in both tests. Rotifer (24-hr) and daphnid (48-hr) acute
toxicity was reported if average survival in the four replicates was significantly
reduced (95 percent probability) from the control.
Physical/Chemical Characteristics-Spills, of the same sediment samples used
in the toxicity testing were analyzed for 13 metals, un-ionized ammonia (in pore
water), total and volatile solids, particle size, and 26 selected trace organics
(organochlorine pesticides and PCBs, Table 2.3).
Additional details for the collection methods, acute toxicity testing protocols and results,
and the physical/chemical analytical results are given in TVA technical report (Moses, Simbeck, and
Wade, 1994). How this sediment quality information was used in the reservoir health evaluations is
described below in Section 3.1.2, Reservoir Sediment Quality Rating Scheme.
Benthic Macroinvertebrate Community Sampling-Benthic macroinvertebrate community
samples were collected in the spring (March and April) of 1993 at 69 locations on the 30 Vital Signs
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reservoirs, Table 2.1. At each sample location, a line-of-sight transect was established across the
width of the reservoir, and Ponar grab samples were collected at ten equally-spaceri locations along
this transect. When rocky substrates were encountered, a Peterson dredge was used. Only those
samples which were collected from the permanently wetted bottom portion of the reservoir (i.e., those
Ponar or Peterson samples collected below the elevation of the minimum winter pool level) were used
to evaluate the condition of the benthic community. Samples were washed in the field, transferred to
a labeled collection jar, and fixed with 10 percent buffered formalin solution. Specimens were sent to
the laboratory where they were sorted, counted, and identified to the lowest practical taxon, typically
genus or species, and reported as number per square meter. Six metrics (Table 3.1) were chosen to
evaluate the benthic macroinvertebrate community as it relates to the overall ecological health of the
reservoir. These metrics and the rating scheme are described in Section 3.1.2, Reservoir Benthic
Community Rating Scheme.
To assess the reproducibility of benthic macroinvertebrate sampling results, replicate
samples were collected at nine of the 69 sampling locations in 1993, with all types of reservoir
locations (i.e., forebay, transition zone, and inflow) included. At each of the replicate sampling
locations, the sampling protocol involved collection of a first set of ten samples, leaving the sampling
location, and then returning as near as possible to the original transect site (on the same day) and
repeating the collection of a second (replicate) set of ten samples. The results from the nine sets of
replicate samples were then evaluated for reproducibility. Benthic macroinvertebrate data are
available in computer-readable form from TVA upon request.
Fish Assemblage Sampling-In the autumn of 1993, electrofishing and/or gill netting data
were collected from 69 locations on the 30 Vital Signs reservoirs to evaluate the fish assemblage,
Table 2.1. Fifteen electrofishing runs (300 meters in length) were made at each location (forebay,
transition or mid-reservoir, and inflow) with all habitats sampled in approximate proportion to their
occurrence at the sampling location. Habitat distinctions were based on major changes in substrate
(e.g., bluff, rip-rap, mud, etc.) and/or presence of cover such as brush or boat docks. Twelve
experimental gill nets were also set overnight at each location covering all habitat types where
conditions permitted. At some inflow locations, flow and/or lack of suitable sites limited the number
of nets that could be set. All fish collected from either electrofishing or gill netting were enumerated,
with length and weight measurements taken on important sport species. Estimated numbers were used
when high densities of fish were encountered during electrofishing. Young-of-the-year (YOY) fish
were counted separately from adults. AH fish measured were inspected for external diseases,
parasites, and anomalies. Twelve metrics (Table 3.3) were chosen to evaluate the fish assemblage as
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it relates to the overall ecological health of the reservoir and are described in Section 3.1.2, Reservoir
Fish Assemblage Rating Scheme.
If the fish assemblage at a particular sampling location appeared to have changed
substantially (up or down) from the previous year, the site was resampled (within one to two weeks)
to assure that sampling conditions were not causing anomalous results. Resample results were used
for two sampling locations (Cherokee Reservoir forebay and Guntersville Reservoir transition zone)
during 1993 fish assemblage evaluations.
All data were recorded on a portable field data logger and downloaded to a personal
computer before being added to the TVA mainframe fisheries data base. Fish assemblage data are
available in computer-readable form from TVA upon request.
Aquatic Macrophvtes-Coverage of aquatic macrophytes was determined from large-scale
(1 inch=600 feet or 1 inch = 1000 feet) color aerial photography flown during maximum submerged
macrophyte coverage (late summer or early fall of 1993). Boat surveys to determine species
composition of the dominant macrophyte communities were conducted at selected sites at the
approximate time of the aerial overflight. Aquatic macrophyte colonies were delineated on mylar
overlays attached to photographic prints, labeled according to species, and areal coverage determined
using an electronic planimeter. Reservoirs flown for aerial photography in 1993 included Kentucky,
Wilson, Wheeler, Guntersville, Nickajack, Chickamauga, Tellico, South Holston, and lakes in the
Beech River project. For reservoirs where aerial photography was unavailable, standard field surveys
and historical information were used to estimate community composition and coverage. Submersed
aquatic plant populations generally are rare in tributary reservoirs because of the wide fluctuations of
water surface elevations associated with their operation for floodwater storage. Known populations
have been extremely small, short-lived, and of little significance.
A detailed summary of TVA's Aquatic Plant Management Program for 1993 and planned
work for 1994 is available in a technical report (Burns, Bates, and Webb, 1994) that is updated and
published annually.
2.1.3 Stream Vital Signs Monitoring
In 1993, Vital Signs stream sampling locations were located on 12 major tributaries to the
Tennessee River (Figure 2.3 and Table 2.2). At each stream sampling location, four types of
information were collected and examined to assess the ecological health of the stream and to provide
information for evaluating the conditions found in the downstream receiving reservoir. These four
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components of stream monitoring (which complement the same four components for reservoir
monitoring) were:
(1) physical/chemical characteristics of water;
(2) acute toxicity and physical/chemical characteristics of
sediment;
(3) benthic macroinvertebrate community sampling; and
(4) fish community sampling.
Phvsical/Chemical Characteristics of Water-In 1993, physical/chemical water quality
characteristics were measured bimonthly (odd numbered months) at 12 stream locations (Table 2.2).
QA/QC methods for the stream water quality sampling activities included: (1) collection and analysis
of duplicate sets of water samples at five stream locations to assess sample collection, laboratory
analysis, and natural sample variability; (2) preparation and analysis of sample container blanks (for
metals and nutrient analyses) each collection day to assess the degree of contamination associated with
the sample bottles and/or the sample handling processes; and, (3) preparation and analysis of sample
filtration blanks (dissolved nutrients and dissolved metals) with each set of filtered samples to assess
the degree of contamination associated with the field sample filtration and handling.
Physical/chemical water quality characteristics measured in 1993 included:
Oil-Site Measurements-flow, temperature, dissolved oxygen, pH,
conductivity, alkalinity, and fecal coliform bacteria; and
Laboratory Measurements-physical analyses (hardness, color, turbidity, total
suspended solids, total dissolved solids, and chemical oxygen demand), nutrient
analyses (organic nitrogen, ammonia nitrogen, nitrite+nitrate nitrogen, total
phosphorus, dissolved orthophosphorus, and total organic carbon), major
cations/anions analyses (calcium, magnesium, sodium, potassium, chloride, and
sulfate), and metal analyses (total and dissolved aluminum, dissolved cadmium,
total and dissolved copper, total and dissolved iron, dissolved lead, total and
dissolved manganese, dissolved nickel, dissolved silver, and total and dissolved
zinc).
The physical/chemical water quality data are stored on EPA's water quality data storage
and retrieval (STORET) system. Methods used to assess physical/chemical quality of each stream
sampling location in regard to the ecological health evaluations are described in Section 3.1.3.
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Acute Toxicity and Physical/Chemical Characteristics of Sediment—During the summer of
1993, an annual sediment and bottom water sample was collected at each of the 12 Vital Signs stream
sampling locations, Table 2.2. Each sediment sample was a composite of at least five surficial
sediment subsamples. At stream sampling locations with shallow and wadable water, subsamples
were collected using clean stainless steel spoons. At sampling locations with deeper water, divers
collected subsamples using one-liter glass jars. The subsamples were composited and thoroughly
mixed to ensure uniform color and texture. At each sampling location the composited sample was
then split for acute toxicity and for physical/chemical analyses. The split samples were placed on ice
immediately and shipped to the Toxicity Testing Laboratory (TI L) at Browns Ferry Nuclear Plant for
toxicity testing and to the Environmental Chemistry Laboratory (ECHE) for chemical and physical
analyses.
Acute toxicity testing and physical/chemical analyses of the split samples were performed
in exactly the same manner as described in Section 2.1.2, Reservoir Acute Toxicity and
Physical/Chemical Characteristics of Sediment. Additional details for the collection methods, acute
toxicity testing protocols and results, and the physical/chemical analytical results are given in a TV A
technical report (Moses, Simbeck, and Wade, 1994b). How this sediment quality information was
used in the stream health evaluations is described in Section 3.1.3, Stream Sediment Quality Rating
Scheme.
Benthic Macroinvertebrate Community Samplinp-Benthic macroinvertebrates were
sampled at the 12 stream sites between mid-May and early July (streamflow conditions permitting) in
order to maximize collection before hatching of winged adults. The benthic sampling sites were
located as close as possible to the corresponding water quality sampling location (Table 2.2), with
exact site selection depending upon the presence of suitable habitat types. Stream habitat in
Tennessee Valley rivers and streams can generally be classified as riffle, run, or pool.
Both quantitative (Hess and Surber) and qualitative (D-net and handpicking) samples were
collected to define relative abundance and species occurrence at each site. Quantitative sampling was
completed in substrate types ranging from rubble to gravel in both riffle and pool habitats.
Qualitative sampling was limited to a maximum of two man-hours per site, or was discontinued when
redundancy in organisms being collected was observed. In total, seven samples were collected per
station. These include: (a) three Hess samples in pools at the head of a riffle in substrate that
contained a light covering of silt; (b) three Surber samples collected in shallow riffle habitat and along
the borders of emergent vegetation (limited to areas where the water did not exceed the depth of the
sampling frame); and (c) a single qualitative sample of bottom fauna organisms using D-nets and
-13-
-------
handpicking from all habitats present. Habitats targeted for qualitative sampling were leaf packs,
woody debris, emergent aquatic vegetation, and boulders.
All specimens were preserved in 10 percent formalin solution and returned to the
laboratory for sorting, enumeration, and identification. Specimens were identified to the lowest
practical taxon, typically genus or species. Twelve metrics, based on a classification system
developed by Kerans et.al (1992), were used to evaluate the stream benthic ecological health
(Table 3.4). Methods used to assess the ecological health of the benthic community at each stream
sampling location are described below (Section 3.1.3, Stream Benthic Community Rating Scheme).
Benthic macroinvertebrate data are available in computer-compatible form from TVA, upon request.
Fish Community Sampling-Fish community sampling was conducted in summer (May-
July) at 11 of the 12 stream sampling locations in 1993, Table 2.2. (The Elk River site was not
sampled.) A boat-mounted electrofishing unit was used for deep pool habitats, and a backpack
electrofishing unit, dip nets, and seine were used for wadable habitats. At each stream site, at least
four general habitats (run, riffle, shallow pool, and deep pool) were sampled until three consecutive
units of sampling effort (seine haul or timed shocking run) produced no additional species per habitat.
Additional habitats were sampled as determined by the field crew leader. Fish specimens that were
difficult to identify were preserved and their identity later confirmed. All fish collected were
enumerated. Numbers were estimated if high densities were encountered during electrofishing.
Young-of-the-year (YOY) fish were counted separately from adults. All fish measured were inspected
for external diseases, parasites, and anomalies.
A modified version of Karr's (1981) index of biotic integrity (IBI) was used to assess the
condition of the resident fish community, Table 3.5. This evaluation scheme is described in Section
3.1.3, Stream Fish Community Rating Scheme. Fish community data are available in computer-
readable form from TVA upon request.
2.2 Use Suitability Monitoring
Use Suitability monitoring provides screening level information on the suitability of
selected reservoir areas and stream reaches in the Tennessee Valley for water contact recreation
(swimmable) and suitability of fish for human consumption (fishable). The use suitability evaluation
is based on results of: (1) bacteriological sampling at recreation areas, and (2) collection and analysis
of fish tissue.
-14-
-------
2.2.1 Bacteriological Sampling
In 1989, TVA began periodically sampling recreation sites in the Tennessee Valley for
fecal coliform bacteria to determine each site's suitability for water contact recreation. In addition to
swimming beaches, many other recreation sites were also included in the program, such as canoe
launch areas, picnic areas, boat ramps, and marinas. This bacteriological sampling program now
includes approximately 260 sites and is designed to sample all locations on a frequency of about once
every other year. Prior to 1993, the sampling frequency was approximately once every five years.
Samples are collected in a manner to conform with state criteria and federal guidelines; at
each site at least ten fecal coliform samples are collected within a 30-day sampling period during the
summer recreation season. QA/QC procedures include running at least one duplicate sample at each
site and preparation and analyses of sample container blanks each collection day to assess degree of
contamination associated with sample containers, handling process, and analytical equipment. The
suitability of a recreation site for water contact recreation is based on EPA guidelines for fecal
coliform bacteria (EPA, 1991).
In 1993, fecal coliform samples were collected in spring and summer at 59 designated
swimming beaches and 14 canoe access sites to evaluate use suitability for whole body water contact
recreation. In addition, 53 informal recreation sites where incidental water contact may occur (e.g.,
boat launch ramps, picnic areas, parks, marinas, etc.), were sampled.
Monthly (April through September) bacteriological samples were collected at 20 forebay
and transition zone locations and four major tributary embayments on the run-of-the-river reservoirs
as part of the basic Vital Signs Reservoir Monitoring (Table 2.1).
All TVA bacteriological sampling data are stored on EPA's water quality data storage and
retrieval (STORET) system. A technical report (Fehring, 1994) provides specific details and
evaluations of TVA's 1993 bacteriological monitoring results, and is available upon request.
2.2.2 Fish Tissue Sampling
In cooperation with Valley states, since 1987 TVA has collected and analyzed fish from
over 80 Tennessee Valley reservoir and stream locations as part of both "screening" and "intensive"
evaluations. In screening studies, composited fillets of indicator fish species (primarily channel
catfish) are analyzed for a wide range of potential contaminants to identify possible problem areas
where intensive investigation may be needed. Intensive studies are conducted on reservoirs or
streams where contamination problems are known or suspected, based on the screening study
information. For intensive studies, individual fillets from several important fish species are analyzed
for specific contaminants to better document the number of species contaminated and level of
-15-
-------
contamination in each species. Intensive studies also include a higher density of sampling locations in
the reservoir or stream of interest to better define the spatial extent of the contamination. The intent
is to provide information that state public health officials can use to determine whether fish
consumption advisories should be issued to protect human health.
Screening Studies-Channel catfish were collected from 16 reservoirs in
autumn of 1992. Fillets were removed, composited by location, and analyzed for
metals, PCBs, and pesticides on EPA's Priority Pollutant List (Table 2.3). During
the preparation process, observations of external and internal conditions of each
fish were recorded along with length, weight, sex, fillet weight, and liver weight.
Intensive Studies-The following six TV A reservoirs were examined
intensively in 1992: Wheeler, Nickajack, Watts Bar, Fort Loudoun, Melton Hill,
and Ocoee No. 1 (Parksville Reservoir). In each case, the contaminant of concern
was PCBs, except for Wheeler, where DDT is the problem. Chlordane was also
of concern in some reservoirs. Fish consumption advisories that recommend either
limiting the quantity of fish eaten or avoiding any consumption are in effect for all
these reservoirs except Ocoee No. 1.
All fish tissue data are stored on EPA's water quality data storage and retrieval (STORET)
system. A technical report (Williams and Dycus, 1993) provides specific details and evaluations of
TVA's 1991 and 1992 fish tissue studies and is available on request.
-16-
-------
Figure 2.1
Schematic of Key Reservoir Sampling Areas
-------
FIGURE 2.2
RESERVOIR VITAL SIGNS MONITORING LOCATIONS -1993
VA
NC
CHTCKAHAUl
23
sc
Ol/NTBJUVILUi >
GEORGIA
ALABAMA
LEGEND
Q RUN-OF-THE-RIVER RESERVOIRS
| | TRIBUTARY, STORAGE RESERVOIRS
See Toble 2 1 For Identificohon Of Somplmg Location*
PRODUCED BY TVA MAPPING SERVICES
-------
FIGURE 2.3
STREAM VITAL SIGNS MONITORING LOCATIONS - 1993
VA
KENTUCKY
TENNESSEE
Q) duck\ river
7) EMC
RIV
jfNfcH RlKPR
Jc^HOLST^ RIV|
NOLKHUCKY RIVgR
NC
DFRENCH BfeOAD RIVER
(3) Sequatchie1 (Driver
"(2) BEAR CREEK
GEORGIA
MISS
ALABAMA
J©N^ITTLE TE^NE^SEE RIVER
SC
LEGEND
(I) DUCK
® SEQUATCHIE © EMORY
@ HOLSTON
@ BEAR
(?) HIWASSEE ® CLINCH
(11) NOL1CHUCKY
® ELK
© L. TENNEESSEE @ POWELL
@ FRENCH BROAD
See Toble 2 2 Tor Idenhftcotion Of Sampling Locotlons
PRODUCED BY TV A MAPPING SERVICES
-------
Table 2.1
1993 Vital Signs Monitoring
Run-of-the-River Reservoirs
—Basic Monitoring Strategy—
Reservei r
Kentucky
Pickwick
I
NJ
O
I
Wilson
Wheeler
Sampling
Locations"
TRM 23.0
TRM 85.0
TRM 200-206
Big Sandy 7.4
TRM 207.3
TRM 2 3 0.0
TRM 253-259
Bear Cr 8.4
TRM 260.8
TRM 273-274
TRM 277.0
TRM 295.9
TRM 347-348
Elk River 6.0
STORET
ID #
202832
477403
477210
476799
016923
017849
016912
016900
017009
017850
1A-FB
1B-TZ
1C-I
1D-E
2A-FB
2B-TZ
2C-I
2D—E
3A-FB
3C-I
4A-FB
4B-TZ
4C-I
4D-E
Reservoir Vital Signs Monitoring Tools
Description1' Uater Quality0
M
M
M
M
M
M
M
M
M
M
Sediment Quality11
Toxicity Phy/Chem
A
A
A
A
A
A
A
A
A
A
A
A
Benthic
Invertebrates'
A
A
A
A
A
A
A
A
A
A
A
A
A
A
Fish Cofnnunitv'
Diversity/RFAI
A
A
A
A
A
A
A
A
A
A
A
A
A
A
Guntersville
TRM 3 50.0
TRM 375.2
TRM 420-424
017261
017522
5A-FB
5B-TZ
5C-I
M
M
A
A
A
A
A
A
A
A
A
A
Nickajack
Chickamuaga
TRM 425.5
TRM 469-470
TRM 472.3
TRM 490.5
TRM 518-529
Hiwassee 8.5
476344
475358
475265
477512
6A-FB
6C-I
7A-FB
7B-TZ
7C-I
7D-E
M
M
M
M
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
-------
Table 2.1 (continued)
1993 Vital Signs Monitoring
Run-of-the-River Reservoirs
—Basic Monitoring Strategy (continued)--
Reservoir Vital Signs Monitoring Tools
Reservoi r
Watts Bar
Sampling
Locations*
TRM 531.0
TRM 560.8
TRM 600-601
CRM 19-22
ST0RET
ID U
475317
476041
Sediment Quality11
Description*1 Water Quality0 Toxicity Phy/Chem
8A-FB
8B-TZ
8C-I
8D-I
M
M
A
A
A
A
Benthic Fish Community
Invertebrates' Pi versi ty/RFAl
A
A
A
A
A
A
A
A
i
Isj
Fort Loudoun
Melton Hill
TRM 605.5
TRM 624.6
TRM 652
CRM 24.0
CRM 4 5.0
CRM 59-66
477404
475603
477064
476194
9A-FB
9B-TZ
9C-I
10A-FB
10B-TZ
10C-I
M
M
M
M
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
Tellico
LTRM 1.0
LTRM 15.0
LTRM 21.0
476260
476456
476295
11A-FB
11B-TZ
M
M
A
A
A
A
A
A
A
A
A
A
Totals 24 25 25
35
35
-------
Table 2.1 (continued)
1993 Vital Signs Monitoring
Tributary Storage Reservoirs
•-Limited Monitoring Strategy—
Reservoir Vital Signs Monitoring Tools
Sampling
ST0RET
Sediment Quality11
Benthic
Fish Community'
Reservoi r
Locations'
ID #
DescriDtion Water Qualitvc
Toxicity
Phv/Chem
Invertebrates'
Diversi ty/RFAI
Norris
CRM 80.0
476009
12A-FB
M
A
A
A
A
CRM 125.0
477186
12B-MR
M
A
A
A
A
PRM 3 0.0
477187
12C-MR
M
A
A
A
A
Cherokee
HRM 53.0
475025
13A-FB
M
A
A
A
A
HRM 76.0
475028
13B-MR
M
A
A
-
A
HRM 91
—
13C-I
-
—
-
A
A
Douglas
FBRM 3 3.0
475081
14A-FB
M
A
A
A
A
FBRM 51.0
477510
14B-MR
M
A
A
-
A
FBRM 61
—
14C-I
-
—
-
A
-
Ft.Pat Henry
SFHR 8.7
477509
15-FB
M
A
A
A
A
Boone
SFHR 19.0
475858
16A-FB
M
A
A
A
A
SFHR 27.0
476221
16B-MR
M
A
A
A
A
WRM 6.5
477511
16C-MR
M
A
A
A
A
South Holston
SFHR 51.0
475859
17A-FB
M
A
A
A
A
SFHR 62.5
475573
17B-MR/I
M
A
A
A
A
Watauga
WRM 37.4
475576
18A-FB
M
A
A
A
A
WRM 4 5.5
477513
18B-MR
M
A
A
A
A
Fontana
LTRM 62.0
370004
19A-FB
M
A
A
A
A
LTRM 81.5
370177
19B-MR
M
A
A
A
A
TkRM 3.0
370162
19C-MR
M
A
A
A
A
-------
Table 2.1 (continued)
1993 Vital Signs Monitoring
Reservoi r
Sampling
Locations*
Tributary Storage Reservoirs
¦Limited Monitoring Strategy (continued)—
STORET
ID U
Reservoir Vital Signs Monitoring Tools
Description1* Water Quality"
Sediment Quality*1
Toxici ty Phy/Cheffl
Benthic
Invertebrates'
Fish Conmunity'
Pi versi ty/RFftl
Hiwassee
HiRM 77.0
HiRM 85.0
HiRM 90
370001
370154
2 OA-FB
2OB-MR
20C-I
M
M
A
A
A
A
A
A
A
A
A
A
i
NJ
OJ
I
Chatuge
Nottely
Ocoee No.l
Blue Ridge
Tims Ford
Bear Creek
Cedar Creek
L.Bear Creek
Beech
Normandy
HiRM 122.0
Shooting Cr 1.5
NRM 2 3.5
NRM 31.0
ORM 12.5
ORM 16.5
TORM 54.1
ERM 135.0
ERM 150.0
BCM 75.0
CCM 2 5.2
LBCM 12.5
BRM 3 6.0
DRM 249.5
370003
370178
120883
120806
475684
130032
477072
475768
017041
017233
017474
475876
477453
21A-FB
2 IB—FB
22A-FB
2 2B-MR
23-FB
24-FB
2 5A-FB
2 5B-MR
26-FB
27 —FB
28—FB
29—FB
30—FB
M
M
M
M
M
M
M
M
M
M
M
M
M
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
A
Totals
33
34
33
34
34
-------
Footnotes
a. BCM - Bear Creek Mile
CRM - Clinch River Mile
FBRM - French Broad River
LBCM - Little Bear Creek Mile
ORM - Ocoee River Mile
TRM - Tennessee River Mile
WRM - Watauga River Mile
BRM - Beech River Mile
DRM - Duck River Mile
HiRM - Hiwassee River Mile
LTRM - Little Tennessee River
PRM - Powell River Mile
ToRM - Toccoa River Mile
PRM - Powell River Mile
CCM Cedar Creek Mile
ERM - Elk River Mile
HRM - Holston River Mile
NRM - Nottely River Mile
SFHR - So Fork Holston River Mile
TkRM - Tuckaseegee River Mile
b. Numbers are keyed to Figure 2.2. FB - forebay; TZ - transition zone; MR - mid-reservoir; I - Inflow; and
E - embayment. MR/I - Sampling location was referred to as an inflow location in the fish community evaluation
(sampling done in autumn at lower reservoir water level elevations); and, as a mid-reservoir location in the
evaluation of the water quality data (sampling done in summer at higher water level elevations).
c. —Basic Monitoring Strategy—
M - monthly water quality surveys (April through September). The surveys includes in situ water column
measurements of temperature, dissolved oxygen, pH, and conductivity; Secchi depth measurements; surface
fecal coliform and photic zone chlorophyll-a samples; and surface and near-bottom water samples for
nutrients (organic nitrogen, ammonia nitrogen, nitrate+nitrite nitrogen, phosphorus, and dissolved ortho
phosphorus), total organic carbon, color, and suspended solids.
—Limited Monitoring strategy—
i M - monthly water quality surveys (April through October). The surveys includes in situ water column
£ measurements of temperature, dissolved oxygen, pH, and conductivity; Secchi depth measurements; and, photic
i zone chlorophyll-a samples. Twice a year (April and August) surface water samples are collected for
nutrients (organic nitrogen, ammonia nitrogen, nitrate+nitrite nitrogen, phosphorus, and dissolved ortho
phosphorus), and total organic carbon. Once a year (August) bottom water samples are collected for ammonia
nitrogen. No samples are collected for fecal coliform, color, and suspended solids.
d. A - annual summer samples of sediment pore water and bottom water are examined for acute toxicity (rotifers
and Ceriodaphnia). At the same time, the sediment is collected and analyzed for metals, total and volatile
solids, particle size, and twenty-six trace organics (organochlorine pesticides and PCBs).
e. A - annual benthic invertebrate samples are collected, enumerated and identified to lowest practical taxon
(genus or species) in the Bpring of year.
f. A - annual electroshocking and gill-netting techniques are used to evaluate the near-shore fish community,
during autumn.
-------
Table 2.2
1993 Vital Signs Monitoring
STREAM VITAL SIGNS MONITORING LOCATIONS, 1993
Tributary Stream
River
Mile
STORET
ID ft
Description
Duck River
26.0
475793
USGS stream gage above
Hurricane Mills, TN
Bear Creek
27.3
017019
TV A stream gage near
Bishop, AL
Elk River
36.5
477330
USGS stream gage at
Veto Road bridge near
Prospect, TN
Sequatchie River
6.3
All 111
Valley Road bridge near
Jasper, TN
Hiwassee River
36.9
477369
East Patty Road bridge
near Benton, TN
Little Tennessee River
94.7
370158
USGS stream gage near
Needmore, NC
Emory River
18.3
475838
USGS stream gage at
Oakdale, TN
Clinch River
159.8
475846
USGS stream gage near
Tazewell, TN
Powell River
65.4
475098
TV A stream gage near
Arthur, TN
Holston River
118.7
475945
TV A stream gage near
Surgoinsville, TN
Nolichucky River
10.3
477150
TV A stream gage at
David Thomas bridge
near Lowland, TN
French Broad River
77.5
475086
US Hwy 411 bridge at
Oldtown, TN
-25-
-------
Table 2.3
1993 Vital Signs Monitoring
PHYSICAL/CHEMICAL MEASUREMENTS - SEDIMENT
Description, units
Detection
Limits
(dry weight)
Sediment
Quality
Guidelines"
Metals and Ammonia
Aluminum, mg/g
1 mg/g
—
Arsenic, mg/kg
1 mg/kg
8 mg/kgb
Cadmium, mg/kg
0.5 mg/kg
6 mg/kgb
Calcium, mg/g
0.5 mg/g
Chromium, mg/kg
10 mg/kg
75 mg/kgb
Copper, mg/kg
2 mg/kg
50 mg/kgb
Iron, mg/g
1 mg/q
—
Lead, mg/kg
5 mg/kg
60 mg/kgb
Magnesium, mg/q
0.5 mg/q
—
Manganese, mq/q
0.1 mq/q
—
Mercury, mg/kg
0.1 mg/kg
1 mg/kgb
Nickel, mg/kg
5 mg/kg
50 mg/kgb
Zinc, mg/kg
10 mg/kg
300 mq/kg
Un-ionized Ammonia (in pore water), pg NH3/1
10 fig/I
200 pg/1
Solids
Total solids, %
0.1%
—
Total volatile solids, %
0.1%
—
Particle size, <0.062 mm diameter, %
0.1%
—
Particle size, <0.125 mm diameter, %
0.1%
—
Particle size, <0.50 mm diameter, %
0.1%
—
Particle size, <2.0 mm diameter, %
0.1%
—
Organochlorine Pesticides and PCB's
Aldrin, tug/kg
10 Mg/kg
10 n<3/kq
a-Benzene Hexachloride (BHC), fjq/kq
10 MQ/kq
10 Mg/kg
/?-Benzene Hexachloride (BHC), fjg/kg
10 jig/kg
10 fjq/kg
7-Benzene Hexachloride (Lindane), /jq/kq
10 Mg/kg
10 Mg/kg
6-Benzene Hexachloride (BHC), Mg/kg
10 Mg/kg
10 pg/kq
Chlordane, ygfkq
10 uq/kq
10 uq/kg
Dieldrin, Mg/kg
10 Mg/kg
10 Mg/kg
p,p DDT, pg/kg
10 Mg/kg
10 pg/kg
p,p DDD, ^g/kg
10 Mg/kg
10 Mg/kg
p,p DDE, Mg/kg
10 Mg/kg
10 Mg/kg
-26-
-------
Table 2.3 (continued)
1993 Vital Signs Monitoring
PHYSICAL/CHEMICAL MEASUREMENTS - SEDIMENT
Description, units
Detection
Limits
(dry weight)
Sediment
Quality-
Guidelines*
Organochlorine Pesticides and PCB's (continued)
a-Endosulfan, pg/kg
10 pg/kg
10 pq/kq
fi-Endosulfan, pq/kq
10 pg/kq
10 pg/kg
Endosulfan Sulfate, pg/kg
10 pq/kq
10 pq/kq
Endrin, pq/kq
10 pq/kq
10 pg/kg
Endrin Aldehyde, pg/kg
10 pg/kg
10 pq/kq
Heptachlor, pq/kq
10 pq/kq
10 pg/kg
Heptachlor Epoxide, pg/kg
10 pg/kg
10 pg/kg
Methoxychlor, pq/kq
10 pg/kg
10 pg/kg
PCB-1221, pg/kg
100 pg/kg
100 pg/kg
PCB-1232, pq/kq
100 pq/kq
100 pg/kg
PCB-1242, pg/kg
100 pg/kg
100 pg/kg
PCB-1248, pq/kq
100 pq/kq
100 pq/kq
PCB-1254, pg/kg
100 pq/kg
100 pg/kg
PCB-1260, pq/kq
100 pq/kq
100 pq/kq
PCB-1016, pq/kg
100 pg/kq
100 pg/kg
PCBs, Total, pq/kq
100 pq/kq
100 pg/kg
Toxaphene, pg/kg
500 f.lq/kq
500 pg/kg
Unless otherwise noted, guidelines are suggested TVA Sediment Quality Guidelines.
" EPA Region V Guidelines for polluted freshwater sediment (EPA, 1977).
-27-
-------
3.0 ECOLOGICAL HEALTH AND USE SUITABILITY DETERMINATION METHODS
3.1 Vital Signs Monitoring
3.1.1 Introduction
The objective of Vital Signs monitoring is to determine the health or integrity of the
aquatic ecosystem within each reservoir or at each stream sampling location. There are no official or
universally accepted guidelines or criteria upon which to base such an evaluation. Consequently, an
evaluation methodology was developed to assess the overall ecological health or condition of each of
the 30 TVA Vital Signs reservoirs and 12 Vital Signs stream monitoring locations. The ecological
health evaluation system combines both biological and physical/chemical information to examine
reservoir and stream health. Five aquatic ecosystem indicators are used for reservoirs: dissolved
oxygen, chlorophyll-a, sediment quality, benthic macroinvertebrates, and fish community; and four
aquatic ecosystem indicators are used for streams: nutrient concentration, sediment quality, benthic
macroinvertebrates, and fish community.
A critical step in developing an ecological health evaluation is deciding for each indicator
what represents good conditions and what indicates poor conditions. This is more easily done for
evaluation of streams because there usually are essentially unaltered reference sites that can be
examined to define "good" conditions for each indicator, for example the various indices of biotic
integrity for fish and benthic stream communities. Because reservoirs are man-made alterations of
natural streams, there are no "reference reservoirs." An alternative approach to "reference
conditions" is required.
3.1.2 Reservoir Ecological Health
Scoring criteria for the reservoir dissolved oxygen and chlorophyll-a indicators were based
on what could be considered a conceptual model. This simply means that the criteria were developed
subjectively, based on several years experience in evaluating biological systems in reservoirs. This
experience has shown that below a threshold level of chlorophyll, primary production is not sufficient
to support an active, biologically healthy food chain. In addition, chlorophyll concentrations above a
higher threshold levels result in undesirable eutrophic conditions. Minimum and maximum
chlorophyll concentrations were selected based on this experience and professional judgment. The
conceptual model for dissolved oxygen criteria for a reservoir is quite complicated due to the
combined effects of flow regulation and the potential for oxygen depletion in the hypolimnion. The
scoring criteria described below attempt a multidimensional approach that includes considering
dissolved oxygen levels both in the water column and near the bottom of the reservoir.
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For the benthic macroinvertebrate and fish community indicators, scoring criteria are
developed based on statistical examination of two or more years of data from TVA reservoirs. For
these indicators, all previously collected TVA reservoir data for a selected community characteristic
(e.g., number of taxa, total abundance, etc.) were ranked and divided into good, fair, and poor
groupings. (Specific procedures used to determine scoring criteria for each grouping are given in
Section 3.1.2, Benthic Community Rating Scheme and Fish Assemblage Rating Scheme.) Data for
the current year of monitoring (e.g., 1993) are then compared to these criteria and scored
accordingly. This approach is valid if the data base is sufficiently large and if it can be safely
assumed that the data base covers the full spectrum of good to poor conditions.
The sediment quality indicator scoring criteria uses a combination of two characteristics:
sediment toxicity to test organisms; and sediment chemical analyses for ammonia, heavy metals,
pesticides, and PCBs (using published guidelines for many of these analytes).
Dissolved Oxygen (DO') Rating Scheme—Oxygen is vital for life. In situations where
funding is limited and only one indicator of reservoir health could be measured, DO would likely be
the indicator of choice. Hutchinson (1975) states that probably more can be learned about the nature
of a lake from a series of oxygen measurements than from any other kind of chemical data. The
presence, absence, and levels of DO in a lake or reservoir both control and are controlled by many
physical, chemical, and biological processes (e.g., photosynthesis, respiration, oxidation-reduction
reactions, bacterial decomposition, temperature). DO measurements coupled with observations of
water clarity (Secchi depth), temperature, nutrients, and some basic hydrologic and morphometric
information provide meaningful insight into the ecological health of a reservoir.
Ideally, a reservoir has near-saturation concentrations of DO throughout the water column
available to fish, insects, and zooplankton for respiration. This is usually the case during winter and
spring, when most reservoirs are well mixed. However, in summer (characterized by more available
sunlight, wanner water temperatures, and lower flows) both thermal stratification and increased
biological activity may combine to produce a greater biochemical demand for oxygen than is
available, particularly in the deeper portions of the reservoir. As a result, summer levels of DO often
are low in the metalimnion and hypolimnion. Hypolimnetic and metalimnetic oxygen depletion are
common, but undesirable, occurrences in many reservoirs, especially storage impoundments. Not
only do lower concentrations of DO in the water column affect the assimilative capacity of a
reservoir, but if they are low enough and/or sustained long enough, they adversely affect the health
and diversity of the fish and benthic communities. Sustained near-bottom anoxia also promotes the
biochemical release of ammonia, sulfide, and dissolved metals into the interstitial pore and
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near-bottom waters. If this phenomenon persists long enough, these chemicals can cause chronic or
acute toxicity to bottom-dwelling animals.
undesirable ecological conditions exist. Values below this level primarily cause adverse impacts on
benthic macroinvertebrate organisms and loss of quality habitat for fish. Historic information for
reservoirs in the Tennessee Valley has shown that the burrowing mayfly (Hexagenia sp.) disappears
from the benthic community at DO concentrations of 2 mg/L and below (Masters and McDonough,
1993). Most fish species avoid areas with DO concentrations below 2.0 mg/L (loss of habitat); fish
growth and reproduction is reduced at these levels, and many highly desirable species such as sauger
and walleye simply cannot survive at such low levels of DO.
The ecological health evaluation considers oxygen concentrations in both the water column
(WCdo) and near the bottom of the reservoir (Bpo). The DO rating at each sampling location
(ranging from 1 "poor" to 5 "good") is based on monthly summer water column and bottom water
DO concentrations. (Summer is defined as a six-month period when maximum thermal stratification
and maximum hypolimnetic anoxia is expected to occur: April through September for the run-of-the-
river reservoirs and May through October for the tributary reservoirs.) The final DO rating is the
average of the water column DO rating and the bottom DO rating:
DO Rating = 0.5 (WC^ rating + rating), where:
WCdo (Water Column DO) Rating-z six-month average of the percent of the
reservoir cross-sectional area (at the location where the sampling was conducted—see
Figure 3.1) that has a dissolved oxygen (DO) concentration less than 2.0 mg/L.
A dissolved oxygen concentration of 2 mg/L was selected as a level below which
Average Cross-Sectional Area
(DO less than 2 mg/L't
<5%
>_5% but <.10%
>10%
WCdo Rating for
Sampling Location
5 (good);
3 (fair);
1 (poor).
Because most state DO water quality criteria for fish and aquatic life specify a
minimum of 5.0 mg/L DO at the 1.5 meter (5 foot) depth, the WC^ rating
was lowered if the measured DO at the 1.5 meter depth at a sampling location
was below 5.0 mg/L at any time. These adjustments were as follows:
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Minimum DO at
1.5 meter depth
Sampling Location
WCdo Rating Change
<5.0 mg/L
< 4.0 mg/L
<3.0 mg/L
etc.
Decreased one unit (e.g., 5 to 4);
Decreased two units (e.g., 5 to 3);
Decreased three units (e.g., 5 to 2);
etc.
Bdq (Bottom DO) Rating-a six month average of the percent of the reservoir
cross-sectional bottom length (at the location where sampling was conducted,
Figure 3.1) that has a DO concentration less than 2.0 mg/L, as follows:
Average Cross-Sectional Length
(DO less than 2 mg/L)
Bqo Rating for
Sampling Location
0%
5 (good);
4
0 to 10%
10 to 20%
20 to 30%
>30%
2
1 (poor).
3 (fair);
The average percent cross-sectional bottom length was computed based on the total
cross-sectional bottom length at average minimum winter pool elevation. In
addition, if anoxic bottom conditions (i.e., 0 mg/L) were observed at a location, the
Bdo rating was lowered one unit, with a minimum rating of 1.
Chlorophyll Rating Scheme-Algae are the base of the aquatic food chain. Consequently,
measuring algal biomass or primary productivity is important in evaluating ecological health. Without
algae converting sunlight energy, carbon dioxide, and nutrients into oxygen and new plant material, a
lake or reservoir could not support other aquatic life. Chlorophyll-a is a simple, long-standing, and
well-accepted measurement for estimating algal biomass, algal productivity, and trophic condition of a
lake or reservoir (Carlson, 1977). Too little primary productivity in reservoirs (mean summer
chlorophyll-a concentrations less than 3 ngfL) indicates an inability to sustain a well-fed, growing,
balanced, and healthy aquatic community. This eventually results in low standing stocks of fish. Too
much primary productivity (mean summer concentrations greater than 15 uglL) often is evidenced by
occasional dense algal blooms, poor water clarity, and the predominance of noxious blue-green algae,
and indicates poor ecological health. The large amounts of algal plant material produced under these
conditions also deplete oxygen concentrations as the algae die and decompose. This can cause or
aggravate problems of low DO in bottom waters.
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Chlorophyll ratings at each sampling location are based on the average summer
concentration of monthly, photic zone chlorophyll-a samples (corrected) collected from April through
September (or October), as shown below. If triplicate samples are collected at a sampling location,
the median value of the triplicate is used in calculating the summer average and the maximum.
* If any single chlorophyll-a sample exceeds 30 fig/L, the value is not included in
calculating the average, but the rating is decreased one unit, (i.e., 5 to 4, or k to 3,
etc.) for each sample that exceeded 30 fig/L.
** If nutrients are present (e.g., nitrate+nitrite greater than 0.05 mg/L and total
phosphorus greater than 0.01 mg/l) but chlorophyll-a concentrations are generally low
(e.g., < 2 M9/L), another/other limiting or inhibiting factors such as toxicity is
likely.- When these conditions exist, chlorophyll is rated 2 (poor).
Sediment Quality Rating Scheme-Contaminated bottom sediments can have direct adverse
impacts on bottom fauna and can often be long-term sources of toxic substances to the aquatic
environment. They may impact wildlife and humans through the consumption of contaminated food
or water or through direct contact. These impacts may occur even though the water above the
sediments meets water quality criteria. There are many sediment assessment methods, but there is no
single method that measures all contaminated sediment impacts at all times and to all biological
organisms (EPA, 1992). TVA's approach combines two sediment assessment methods—one
biological, the other chemical—to evaluate sediment quality. TVA's scoring criterion is based on
ratings for the toxicity of sediment pore water (ST0X) to test organisms, and the chemical analysis of
sediment (Schm) for heavy metals, PCBs, organochlorine pesticides, and un-ionized ammonia
(Table 2.3). The final sediment quality score or rating is the average of these two ratings:
Sediment Quality Rating = 0.5 (SroX rating + SchM rating), where:
Smx (Sediment Toxicity) /taftn£-Sediment toxicity is evaluated using both
Rotox® (rotifer Brachionus calvciflorus survival) and daphnid (Ceriodaphnia dubial
acute tests. The acute toxicity evaluations entail the exposure of these organisms
(zooplankton) to interstitial pore water from sediment. The survival rates of the
organisms are based on the average survival in four replicates of five individuals
Average Chlorophyll-a
Concentration*
Sampling Location
Chlorophyll Rating
Less than 3 /ig/L
3 to 10 /ig/L
10.1 to 15 /xg/L
Greater than 15 /ig/L
3 (fair);**
5 (good);
3 (fair);
1 (poor).
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each, compared to a control. If average survival is significantly reduced (95
percent probability) from the control, the sample is considered to be toxic.
Sampling locations are rated as follows:
Sampling Location Percent Survival of
STOX Rating Ceriodaphnia and/or Branchionus
5 (good) Survival not significantly different than
control and greater than or equal to 80
percent for both species, (i.e., no
significant toxicity);
3 (fair) Survival not significantly different from
control, but less than 80 percent survival
for either species; or
1 (poor) Survival of either organism significantly
less than control, (i.e., significant toxicity).
Sqhm (Sediment Chemistry) Rating—Splits of the same sediment used in the
sediment toxicity testing are analyzed for heavy metals, organochlorine pesticides
and PCBs, and un-ionized ammonia. Sediment chemistry ratings are based on:
(a) concentrations of heavy metals (Cd, Cr, Cu, Pb, Hg, Ni, and Zn) that exceed
freshwater sediment guidelines (EPA, 1977); (b) detectable amounts of PCBs or
pesticides; and (c) concentrations of un-ionized ammonia in pore water above
200 ng NH3/L. Each sampling location is rated as follows:
Sampling Location
Schm Rating Sediment Chemistry*
5 (good) No analytes exceed guidelines;
3 (fair) One or two analytes exceed guidelines;
1 (poor) Three or more exceed guidelines.
* Analytes (i.e., heavy metals, pesticides, PCBs arid ammonia) and guidelines are
listed in Table 2.3.
Benthic Community Rating Scheme-Six community characteristics (or metrics), with
scoring criteria specific to either run-of-the-river or storage reservoirs, are used to evaluate the
ecological health of the benthic macroinvertebrate community (Table 3.1). These characteristics are:
1. Taxa Richness—The number of different taxa present. An increase in total
taxa or taxa richness is used to indicate better conditions than low taxa
richness.
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2. Longed-Lived species—The number of taxa CCorhicula. Hexagenia. mussels,
and snails) present. These organisms are long-lived and their presence indicate
conditions which allow long-term survival.
3. EPT-The number of different taxa within these orders (Ephemeroptera-
mayflies, Plecoptera-stoneflies, and Tricoptera-caddisflies). Higher numbers
of this metric indicate good water quality conditions in streams. A similar use
is incorporated here despite expected lower numbers in reservoirs than in
streams.
4. Proportion as Chironomidae-The percent of the total organisms in the
sample that are chironomids. A higher proportion indicates poor conditions.
5. Proportion as Tubificidae-The percent of the total organisms present that are
tubificids. A higher proportion indicates poor quality.
6. Proportion as Dominant Taxa-The percent of total organisms present that
are members of the dominant taxon. This metric is used as an evenness
indicator. A large proportion comprised by one or two taxa indicates poor
conditions.
Specific scoring criteria were developed for each of the six metrics for both run-of-the-
river reservoirs and tributary reservoirs. And given the substantial habitat differences among
forebays, transition zones/mid-reservoirs, and inflows, specific scoring criteria were also developed
for each of these areas (Table 3.1). Data handling also differed among the metrics. Metric 1, taxa
richness, is the average total number of taxa per sample at each site. Metrics 2 and 3 are handled
similarly. For Metric 4 the proportion of chironomids in each sample is calculated, then these
proportions are averaged for a location. An alternative that was considered was to sum the number of
chironomids in all samples and divide by the sum of the total individuals for all samples. The
approach selected gives equal weight to all samples regardless of sample size or sampling gear (Ponar
or Peterson dredge). This eliminates the bias introduced in the alternate approach when one sample at
a site has an exceptionally large or small density. Metric 5 is calculated in the same way. Metric 6,
proportion as dominant taxa, is calculated as proportion for each sample, similar to computations for
Metrics 4 and 5. The proportion is calculated for the dominant taxon in each sample even if the
dominant taxon differed among the samples at a site. This allows more discretion to identify
imbalances at a site than developing an average for a single dominant taxon for all samples at the site.
A quantitative approach is used to evaluate the benthic macroinvertebrate community
information. The range of values for each of the six metrics found in the available data base (in this
case, all the 1991, 1992, and 1993 Vital Signs benthic monitoring data) serves as the basis for
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evaluation criteria. For each metric at each of the three reservoir sampling zones (forebay, transition
zone/mid-reservoir, and inflow) and two reservoir types (run-of-the-river and tributary) the data base
values are divided into three groups using Ward's minimum variance analysis (SAS, 1989). This
procedure places observations into three homogenous groups of approximate equal size. The groups
are sorted and categorized as poor, fair, or good. Scoring criteria represent values between the
highest and the lowest value in each group (Table 3.1). Results for each metric for the current year
are then compared with these criteria and assigned quantitative values of 1 (poor), 3 (fair), or 5
(good) if they fall within the bottom-, middle-, or top-group, respectively. This results in a minimum
score of 6 if all metrics at a site are poor, and a maximum score of 30 if all metrics are good.
Detailed scoring criteria for each metric are provided in Table 3.1.
Metrics are summed for each reservoir sampling site to yield a final benthic score and are
evaluated as follows:
Sum of Benthic
Community Metric Sampling Location
Scores Benthic Rating
6-10 1 (poor)
11-15 2
16-20 3 (fair)
21-25 4
26-30 5 (good)
Fish Assemblage Rating Scheme-In 1993, a Reservoir Fish Assemblage Index (RFAI)
(Hickman et.al, 1994) was used to rate fish assemblages as they relate to the overall ecological health
of the reservoir. The RFAI is based on 12 metrics with scoring criteria specific to either
run-of-the-river or storage reservoirs. Scoring criteria also are specific for the type of sample
location within reservoirs—forebay, transition zone/mid-reservoir, or inflow; anil for the type of
sampling gear used (i.e., electrofishing for littoral fish communities and gill netting for pelagic fish
communities). The metrics address the following 12 reservoir fish assemblage characteristics. Table
3.2 lists the trophic, reproductive, and tolerance designations of fish species collected as part of Vital
Signs Reservoir Monitoring activities.
Species Richness and Composition
1. Total number of species—Greater numbers of species are considered
representative of healthier aquatic ecosystems. As conditions degrade, numbers
of species at a site decline.
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2. Number of piscivore species-Higher diversity of piscivores is indicative of
better quality environment.
3. Number of sunfish species-Lepomid sunfish (excludes black basses, crappies,
and rock bass) are basically insectivores, and high diversity of this group is
indicative of reduced siltation and high sediment quality in littoral areas.
4. Number of sucker species-Suckers are also insectivores but inhabit the pelagic
and more riverine sections of reservoirs. This metric closely parallels the
lithophilic spawning species metric (Metric 10) and may be deleted from future
RFAI calculations.
5. Number of intolerant species-This group is made up of species that are
particularly intolerant of habitat degradation. Higher densities of intolerant
individuals represent better environmental quality.
6. Percentage of tolerant individuals (excluding Young-of-Year)-This metric
signifies poorer quality with increasing proportions of individuals tolerant of
degraded conditions.
7. Percent dominance by one species-Ecological quality is considered reduced if
one species dominates the resident fish community.
Trophic Composition
8. Percentage of individuals as omnivores-Omnivores are less sensitive to
environmental stresses due to their ability to vary their diets. As trophic links
are disrupted due to degraded conditions, specialist species such as insectivores
decline while opportunistic omnivorous species increase in relative abundance.
9. Percentage of individuals as insectivores-Due to the special dietary
requirements of this group of species and the limitations of their food source in
degraded environments, proportion of insectivores increases with environmental
quality.
Reproductive Composition
10. Number of lithophilic spawning species—Lithophilic broadcast spawners are
selected due to their sensitivity to siltation. Numbers of lithophilic spawning
species increase in reservoirs providing suitable conditions reflective of good
environmental quality.
Abundance and Fish Health
11. Total catch per unit effort (number of individuals)—This metric is based upon
the assumption that high quality fish assemblages support large numbers of
individuals.
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12. Percent individuals with anomalies—Incidence of diseases, lesions, tumors,
external parasites, deformities, blindness, and natural hybridization are noted for
all fish measured, with higher incidence indicating poor environmental
conditions.
Each metric is assigned a score of 5, 3, or 1 - representing "good," "fair," or "poor,"
conditions, respectively. Due to the distinct habitat differences among reservoirs and sampling
locations-and the differences in fish assemblages they support-different scoring criteria are used for
each of the 12 metrics for: (a) each reservoir type (i.e., run-of-the-river and tributary storage
reservoirs); (b) each sampling location (forebay, transition/mid-reservoir, and inflow); and (c) each
type of sampling gear used to collect the fish data (electrofishing and gill netting). Scoring criteria by
reservoir type, by sampling location, and by sampling gear type are listed for each of the 12 fish
community metrics in Table 3.3. There is not yet enough information for inflow sampling locations
on tributary reservoirs to establish criteria for the fish community metrics at these particular sites.
The average of the sum of the electrofishing scores and the sum of the gill netting scores
results in the Reservoir Fish Assemblage Index (RFAI) for each sampling location. The range of
"attainable" RFAI values could be from 12 (if all metrics scored 1) to 60 (if all metrics scored 5).
This range of RFAI values, from 12 to 60, is divided into five equal groupings to evaluate the overall
health of the fish assemblage at each sampling location, as follows:
RFAI Sampling Location
Score Rating
12-21 1 (poor)
21-31 2
32-41 3 (fair)
42-51 4
52-60 5 (good)
A discussion of the development of the RFAI and results of the fish evaluations for the
1991-1993 Vital Signs Monitoring data are available in TVA technical reports (Scott, et. al, 1992;
Brown, et. al, 1993; and Hickman et. al, 1994).
Overall Reservoir Health Determination-The overall ecological evaluation methodology
combines the five previously discussed aquatic ecosystem indicators (DO, chlorophyll, sediment
quality, benthic macroinvertebrates, and fish assemblage) into a single numeric value. This facilitates
spatial comparisons among reservoirs and temporal comparisons for a reservoir through time.
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The first step in determining an overall reservoir health score is to sum the ratings for all
indicators (ranging from 1-poor to 5-excellent) at a sample site. The number of indicators monitored
at each site varies. Generally, all five indicators are included; however, this is not always the case.
For example, chlorophyll and sediment quality are not monitored at the inflows on run-of-the-river
reservoirs because in situ plankton production of chlorophyll does not occur significantly in that part
of a reservoir and because sediments do not accumulate there. The number of sites per reservoir also
varies from one (the forebay) in small tributary reservoirs to four (forebay, transition zone, inflow,
and embayment) in selected run-of-the-river reservoirs. As a result, the number of ratings vary from
five to 18 for the 30 reservoirs monitored in 1993. Specific information on what indicators were
sampled in each reservoir is in Table 2.1.
To arrive at an overall health evaluation for a reservoir, the sum of the ratings from all
sites are totaled, divided by the maximum potential ratings for that reservoir, and expressed as a
percentage. For example, a small reservoir with only one sample site, the minimum health evaluation
would be 20 percent (all five indicators rated poor-1 for a total score of 5 divided by the maximum
possible total of 25) and the maximum would be 100 percent (all five indicators rated good-5). This
same range of 20 to 100 percent applies to all reservoirs regardless of the number of sample sites,
and the same calculation process is used.
The next step is to divide the 20-100 percent scoring range into categories representing
good, fair, and poor ecological health conditions. This has been achieved as follows:
1. Results are plotted and examined for apparent groupings.
2. Groupings are compared to known, a priori conditions (focusing on reservoirs
with known poor conditions), and good-fair and fair-poor boundaries were
established subjectively.
3. The groupings are compared to a trisection of the overall scoring range. A
scoring range is adjusted up or down a few percentage points to ensure a
reservoir with known conditions falls within the appropriate category. This is
done only in circumstances where a nominal adjustment is necessary.
Based on these considerations, during the first two years of development (1991-1992),
scoring ranges were as follows:
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Fair
Good
Run-of-the-river reservoirs <52% >52-72% >72%
Tributary, storage reservoirs <56% >56-72% >72%
The difference in the poor scoring range between the two types of reservoirs is due to the
fact that two storage reservoirs with known poor conditions rated slightly higher than the boundary
for the lower (poor) grouping on the run-of-the-river reservoirs. Hence, the high end of the lower
scoring range for storage reservoirs was shifted upward from 52 to 56 percent to accommodate these
reservoirs with known poor conditions.
Based on the experience gained in developing this evaluation process, review of the
evaluation scheme by other state and federal professionals, and results of another year of monitoring,
slight modifications were made in the original evaluation process and the numerical scoring criteria
for each of the five ecological health indicators. In 1993, run-of-the-river reservoirs with overall
scores greater than 72 percent were evaluated as "good"; those between 52 percent and 72 percent
were rated "fair"; and those whose overall scores were less than 52 percent were rated "poor."
Similarly, in 1993, tributary storage reservoirs were evaluated as "good" if their overall reservoir
percentage was greater than or equal to 72 percent; "fair" if its overall reservoir percentage was
between 57 percent and 72 percent; and "poor" if its overall reservoir percentage was less than 57
percent. The 1993 scoring ranges were:
Poor Fair Good
Run-of-the-river reservoirs <52% 52-72% >72%
Tributary, storage reservoirs <57% 57-72% >72%
Two examples that illustrate the overall reservoir health evaluation methodology are
presented in Tables 3.6 and 3.7. Wilson Reservoir (Table 3.6) has five aquatic health indicators at
one location and three indicators at another location. Cherokee Reservoir (Table 3.7) has five aquatic
health indicators at one location and four indicators at another location.
3.1.3 Stream Ecological Health
An evaluation methodology similar to the Reservoir Ecological Health Evaluation
(Section 3.1.2) is used to assess the overall ecological health at each of the 12 stream monitoring
locations. Particular emphasis is given to the relationship between the conditions found at the stream
sampling site and the potential for impacts on conditions in the downstream reservoir. The following
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overview summarizes TVA's stream ecological health evaluation methodology. The evaluations are
based on four aquatic health indicators: (1) total phosphorus (as a measure of nutrient enrichment and
potential for excessive algal productivity); (2) sediment quality; (3) benthic community; and (4) fish
community.
At each stream sampling location the four aquatic health indicators are rated as "good,"
"fair," or "poor." Equal weights are given to each indicator, and each rating is assigned a numeric
value of 1, 3, or 5 corresponding to "poor," "fair," or "good." The four scores are summed to
produce an overall stream health evaluation at the sampling location ranging from 4 to 20. A stream
sampling location with an overall rating of 9 or less (<45 percent) was rated "poor"; 10 to 15 (50
percent to 75 percent) "fair"; and 16 to 20 (80 percent to 100 percent) "good."
Nutrient Concentration Rating Scheme-Phosphorus is an essential nutrient required by
aquatic plants for photosynthesis and growth. In freshwater ecosystems phosphorus is most often the
nutrient least available to plants relative to their needs, and thus can limit algal productivity. When
present in excess of critical concentrations, in combination with sufficient nitrogen phosphates, it can
stimulate algae and other aquatic plant growth, sometimes to an undesirable level that interferes with
water uses. To prevent the development of biological nuisances and to control accelerated phosphorus
loading for the protection of downstream receiving waterways, EPA recommends a guideline for
maximum total phosphorus concentration of 0.10 mg/L for streams or flowing waters and 0.05 mg/L
at the point where any stream enters a lake or reservoir (EPA, 1986). These guidelines are used as
the basis to evaluate total phosphorus concentrations in Tennessee Valley streams (average of 6
samples per year):
Average Total Phosphorus Sampling Location
Concentration* Nutrient Enrichment Rating
Less than 0.05 mg/L 5 (good);
0.05 to 0.10 mg/L 3 (fair);
Greater than 0.10 mg/L 1 (poor).
* In addition, waters that receive high nitrogen concentrations in the presence of
sufficient phosphorus often stimulate the growth of algae and other aquatic plants to an
undesirable extent. High average (relative to the majority of Valley streams)
nitrate+nitrite nitrogen concentrations greater than 0.65 mg/L resulted in lowering a
rating from "good" to "fair" or from "fair" to "poor," as appropriate.
Sediment Quality Rating Scheme-The stream sediment quality evaluation methodology is
the same as for reservoir sediment quality. The scoring criterion is based on ratings for the acute
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toxicity of sediment pore water (ST0X) to both Rotox® (rotifer, Brachionus calvciflorus survival) and
daphnid (Ceriodaphnia dubia). and the chemical analysis of sediment (Schm) for heavy metals, PCBs,
organochlorine pesticides, and un-ionized ammonia. The final sediment quality score or rating is the
average of these two ratings. (Details are given in Section 2.1.2, Reservoir Sediment Quality Rating
Scheme.)
Sediment Quality Rating = 0.5 (St0x rating + SCHM rating).
Benthic Community Rating Scheme-A modified version of the benthic index of biotic
integrity (BIBI) (Kerans et. al, 1992) is used to rate the condition of the benthic community. Twelve
benthic community attributes such as total taxa richness and richness of specific taxa, relative
abundance of functional and trophic groups and certain tolerant organisms, and total abundance are
used. Each of the 12 metrics is scored based on best expected conditions at reference sites supporting
healthy benthic communities and good water quality. At each site three Surber (riffle), three Hess
(pool), and one qualitative sample were taken. EPT, intolerant snail and mussel species metrics were
computed pooling all qualitative and quantitative samples. Total abundance was computed pooling all
quantitative samples. The remaining metrics were computed separately for each quantitative sample
at a site.
Taxa Richness and Community Composition
1. Taxa richness
2. Occurrence of intolerant snail and mussel species*
3. Number of mayfly (Ephemeroptera) taxa
4. Number of stonefly (Plecoptera) taxa
5. Number of caddisfly (Trichoptera) taxa
6. Total number of EPT taxa*
7. Percentage as oligochaetes
8. Percentage in the two most dominant taxa
Trophic and Functional-Feeding Group
9. Percent as omnivores and scavengers
10. Percent as collector-filterers
11. Percent as predators
Abundance
12. Total abundance of individuals (combined quantitative samples, lower score given
for extremely low values or extremely high values)
* Metric applied to qualitative and quantitative samples combined. All other metrics applied to individual
quantitative samples and resultant scores averaged.
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Values obtained for each of these metrics are scored (1-poor, 3-fair, or 5-good) against
best expected value based on data from reference sites supporting healthy fish communities and
having good water quality (Table 3.4). Metric scores are then summed to produce an index ranging
from 12 to 60. The resultant benthic community index for each stream location is classified as
"poor" (<30), "fair" (34-44), or "good" (>45). If the index score falls between 30-33, professional
judgment is used to categorize the benthic community as either poor or fair.
Fish Communitv-A modified version of Karr's (1981) index of biotic integrity (IBI) is
used to assess the condition of the resident fish community at 11 of the 12 stream monitoring
locations. (Fish community sampling was not conducted on the Elk River in 1993.) An index and
rating are produced for each site by applying the following 12 metrics.
Species richness and composition
1. Number of native species
2. Number of darter species
3. Number of native sunfish species (excluding Micropterus sp.)
4. Number of sucker species
5. Number of intolerant species
6. Percentage of individuals as tolerant species
Trophic structure
7. Percentage of individuals as omnivores
8. Percentage of individuals as specialized insectivorous minnows and darters
9. Percentage of individuals as piscivores
Fish abundance and condition
10. Catch rate (average number per unit of sampling effort, seine hauls and shocking
runs)
11. Percentage of individuals as hybrids
12. Percentage of individuals with poor condition, injury, deformity, disease, or other
anomaly
Actual values obtained for each of these metrics are scored (1-poor, 3-fair, or 5-good)
against values expected under pristine conditions (i.e., best expected value, Table 3.5). The 12
metric scores are then summed to produce an index ranging from 12 to 60, and the fish community at
the stream sampling location is rated as "poor" (index <36), "fair" (index 40-44), or "good" (index
>46). Professional judgment is involved when a fish community index falls between ratings. For
example, an index of 38 falls between "poor" and "fair" and would be either "poor" or "fair"
-43-
-------
depending on the judgment of the biologist taking the sample. Judgment usually is influenced by
which of the 12 metrics rates poorest, condition of the coexisting macroinvertebrate community, or
previous 161 ratings obtained for the site.
3.2 Use Suitability
3.2.1 Bacteriological Quality Evaluation
Each of the seven Valley states follows the EPA guideline of using a geometric mean fecal
coliform concentration of 200 colonies per 100 milliliters (200/100 mL) of water to determine use
suitability for whole body water contact recreation (EPA, 1991). Six of the states use an additional
fecal coliform criterion to determine if a site is unsuitable for water contact recreation; either a
percentage of samples exceeds 400/100 mL, or a maximum concentration of 1000/100 mL for any
one sample.
TVA reports on the bacteriological condition of stream and reservoirs throughout the
Valley in its publication RiverPulse using the following three categories:
Posted by the State:
+ The state has issued a public advisory against water contact and has posted
signs near the body of water with the advisory.
+ Each area presently posted exceeds the geometric mean criterion due to a
known human source of contamination.
Exceeds Criterion:
+ The geometric mean of a minimum of ten fecal coliform bacteria samples
collected by TVA over a period of not more than 30 days from May through
September exceeds 200/100 mL.
+ Each site identified is believed to exceed criterion due to animal waste.
Meets Criterion:
+ The geometric mean of a minimum of ten fecal coliform bacteria samples
collected by TVA over a period of not more than 30 days from May through
September is less than 200/100 mL.
TVA recommends no water contact recreation for at least two days following rain events at
locations which only partially support water contact because of the bacteria which are washed into the
-44-
-------
water. In addition, TVA recommends no water contact recreation in the immediate vicinity of
wastewater discharges regardless of what fecal bacteria data show, because of the possibility of
mechanical breakdowns and sewage bypasses or overflows.
3.2.2 Fish Tissue Consumption Advisories
TVA and state agencies coordinate with one another in conducting fish tissue studies in the
Tennessee Valley. There is a shared interest in the status of TVA reservoirs as important and
valuable resources. As the government organizations responsible for regulatory and public health
decisions related to lakes and streams! state agencies are interested in knowing both the ecological
health of Valley reservoirs and whether the fish are safe to eat.
Prior to initiating sample collections each autumn, TVA and involved Valley state agencies
meet to discuss the previous year's results and decide appropriate direction for further study. The
group reaches agreement on species to collect, locations to sample, and the agencies responsible for
conducting each part of the work. TVA provides its results to the appropriate states, then the states
take action to protect public health. This usually involves deciding whether to issue an advisory
against consuming selected species or age classes of fish. TVA's role in this process is to provide
accurate results, to provide consultation to the state(s) as appropriate, and support the state's
decisions.
-45-
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Figure 3.1
Cross-section of Tellico Reservoir Forebay Showing Areas where Summer DO Concentrations
averaged less than or equal to 2 mg/l.
Distance across Reservoir (ft)
-------
Table 3.1
1993 Vital Signs Monitoring
Reservoir Benthic Macroinvertebrate Community metrics and scoring criteria developed for Tennessee Valley
Reservoirs, with a score of 5 representing highest quality, and a score of 1 the poorest.
Run-of-the-River Reservoirs
Benthic Community
Metrics
Forebay
Transition
Inflow
5
3
1
5
3
1
5
3
1
Taxa Richness
>6.1
4.6-6.1
<4.6
>7.6
6.5-7.6
<6.5
>8.0
5.2-8.0
<5.2
Long Lived Species
>1.2
0.35-1.2
<0.35
>2.4
1.3-2.4
<1.3
>1.9
1.3-1.9
<1.3
EPT (mayfly, stonefly, caddisfiy)
>0.95
0.5-0.95
<0.5
>0.95
0.6-0.95
<0.6
>1.4
0.6-1.4
<0.6
% Chironomidae
<30
30-45
>45
<25
25-40
>40
<10
10-30
>30
% Tubificidae
<25
25-50
>50
<20
20-40
>40
<11
11-25
>25
% Dominant Taxa
<75
75-90
>90
<65
65-70
>70
<70
70-80
>80
Tributary Reservoirs
Benthic Community
Metrics
Forebay
Mid-Res/Inflow
5
3
1
5
3
1
Taxa Richness
>4.3
2.3-4.3
<2.3
-
-
-
>6.2
3.4-6.2
<3.4
Long Lived Species
>1.0
0.15-1.0
<0.15
-
-
-
>0.45
0.15-0.45
<0.15
EPT (mayfly, stonefly, caddisfiy)
>0.35
0.15-0.35
<0.15
-
-
-
>0.3
0.09-0.3
<0.09
% Chironomidae
<30
30-50
>50
-
-
-
<25
25-70
>70
% Tubificidae
<30
30-60
>60
-
-
-
<45
45-75
>75
% Dominant Taxa
<78
78-91
>91
-
-
-
<70
70-80
>80
-47-
-------
Table 3.2
1993 Vital Signs Monitoring
Core fish species list with trophic tolerance, and reproductive designations (*)
for use in Reservoir Fish Assemblage Index (RFAI) for TV A reservoirs, 1993.
Species
Trophic
Guild
Tolerance
Lithophilic
Spawner
Chestnut lamprey
PS
L
Spotted gar
PI
Longnose gar
PI
TOL
Shortnose gar
PI
TOL
Bowfin
PI
American eel
PI
Skipjack herring
PI
INT
Gizzard shad
OM
TOL
Threadfin shad
PL
Mooneye
IN
L
Chain pickerel
PI
Central stoneroller
HB
Common carp
OM
TOL
Goldfish
OM
TOL
Silver chub
IN
INT
Golden shiner
OM
TOL
Emerald shiner
IN
Ghost shiner
IN
Spotfin shiner
IN
Mimic shiner
IN
INT
Steelcolor shiner
IN
Pugnose minnow
IN
Bluntnose minnow
OM
Fathead minnow
OM
Bullhead minnow
IN
River carpsucker
OM
Quillback
OM
Northern hog sucker
IN
INT
L
Smallmouth buffalo
OM
Bigmouth buffalo
PL
Black buffalo
OM
Spotted sucker
IN
INT
L
Silver redhorse
IN
L
Shorthead redhorse
IN
L
River redhorse
IN
INT
L
Black redhorse
IN
INT
L
Golden redhorse
IN
L
-48-
-------
Table 3.2 (continued)
1993 Vital Signs Monitoring
Core fish species list with trophic tolerance, and reproductive designations (*)
for use in Reservoir Fish Assemblage Index (RFAI) for TVA reservoirs, 1993.
Species
Trophic
Guild
Tolerance
Lithophilic
Spawner
Blue catfish
OM
Black bullhead
OM
TOL
Yellow bullhead
OM
TOL
Brown bullhead
OM
TOL
Channel catfish
OM
Flathead catfish
PI
Blackslripe topminnow
IN
Blaclcspotted topminnow
IN
Mosquitofish
IN
TOL
Brook Silverside
IN
White bass
PI
L
Yellow bass
PI
L
Rock bass
PI
INT
Redbreast sunfish
IN
TOL
Green sunfish
IN
TOL
Warmouth
IN
Orangespotted sunfish
IN
Bluegill
IN
Longear sunfish
IN
INT
Redear sunfish
IN
Spotted sunfish
IN
Smallmouth bass
PI
Spotted bass
PI
Largemouth bass
PI
White crappie
PI
Black crappie
PI
Yellow perch
IN
Logperch
IN
L
Sauger
PI
L
Walleye
PI
L
Freshwater drum
IN
'Designations:
Trophic: herbivore (HB), parasitic (PS), planktivore (PL),
omnivore (OM), insectivore (IN), piscivore (PI)
Tolerance: tolerant (TOL), intolerant (INT)
Lithophilic spawning species (L)
-49-
-------
Table 3.3
1993 Vital Signs Monitoring
Reservoir Fish Assemblage Index metrics and scoring criteria developed for TV A Run-of-the-River reservoirs.
Scoring reflects fish community quality, with a score of 5 representing highest quality, and a score of 1 the poorest.
Metric
Gear*
Inflow
Transition
Forebay
5
3
1
5
3
1
5
3
1
Species Richness
1. Total species
E
>27
21-27
<21
>25
19-25
<19
>25
21-25
<21
G
-
-
~
>21
18-21
<18
>19
17-19
<17
2. Piscivore species
E
>9
5-9
<5
>8
6-8
<6
>8
7-8
<7
G
-
-
-
>9
7-9
<7
>9
8-9
<8
3. Sunfish species
E
>4
3-4
<3
>5
4-5
<4
>5
4-5
<4
G
-
-
-
>2
2
<2
>2
2
<2
4. Sucker species
E
>5
4-5
<4
>3
2-3
<2
>2
2
<2
G
-
-
-
>3
2-3
<2
>3
2-3
<2
5. Intolerant species
E
>4
3-4
<3
>2
2
<2
>2
2
<2
G
-
-
--
>2
2
<2
>2
2
<2
6. Percent tolerant
individuals
E
<40
40-60
>60
<30
30-60
>60
<30
30-60
>60
G
-
-
-
<20
20-35
>35
<25
25-40
>40
7. Percent dominance
by one species
E
<30
30-50
>50
<40
40-60
>60
<40
40-60
>60
G
-
-
-
<30
30-40
>40
<30
30-40
>40
Trophic Composition
8. Percent individuals
as ommvores
E
<30
30-60
>60
<30
30-60
>60
<30
30-60
>60
G
-
-
-
<35
35-55
>55
<35
35-50
>50
9. Percent individuals
as insectivores
E
>50
30-50
<30
>70
40-70
<40
>60
30-60
<30
G
-
-
-
>15
5-15
<5
>10
5-10
<5
Reproductive Composition
10. Lithophilic spawning
species
E
>7
5-7
<5
>4
3-4
<3
>5
4-5
<4
G
-
-
-
>5
5
<5
>5
5
<5
Abundance and Health
11. Total catch per unit
effort
E
>120
70-120
<70
>130
70-130
<70
>130
80-130
<80
G
-
-
~
>30
15-30
<15
>40
20-40
<20
12. Percent individuals
with anomalies
E
<1
1-3
>3
<1
1-3
>3
<1
1-3
>3
G
-
-
-
<1
1-3
>3
<1
1-3
>3
* E=electrofishing; G=gill netting
-50-
-------
Table 3.3 (continued)
1993 Vital Signs Monitoring
Reservoir Fish Assemblage Index metrics and scoring criteria developed for TVA Tributary reservoirs. Scoring
reflects fish community quality, with a score of 5 representing highest quality, and a score of 1 the poorest.
Metric
Gear*
Inflow
Mid-Reservoir
Forebay
5
3
1
5
3
1
5
3
1
Species Richness
1. Total species
E
-
-
-
>17
15-17
<15
>25
21-25
<21
G
-
-
-
>16
13-16
<13
>14
11-14
<11
2. Piscivore species
E
~
-
-
>6
5-6
<5
>5
4-5
<4
G
-
-
-
>7
7
<7
>6
5-6
<5
3. Sunfish species
E
-
--
-
>3
3
<3
>4
3A
<3
G
~
-
~
>1
1
<1
>1
1
<1
4. Sucker species
E
--
-
--
>3
2-3
<2
>2
2
<2
G
-
-
-
>3
2-3
<2
>3
2-3
<2
5. Intolerant species
E
-
-
-
>2
2
<2
>3
2-3
<3
G
-
--
-
>1
1
<1
>1
1
<1
6. Percent tolerant
individuals
E
~
-
--
<20
20-40
>40
<20
20-40
>40
G
--
-
--
<20
20-40
>40
<20
20-40
>40
7. Percent dominance
by one species
E
-
-
-
<40
40-60
>60
<40
40-60
>60
G
--
-
-
<30
30-50
>50
<30
30-50
>50
Trophic Composition
8. Percent individuals
as ommvores
E
-
-
~
<15
15-30
>30
<20
20-40
>40
G
--
-
-
<30
30-50
>50
<30
30-50
>50
9. Percent individuals
as insectivores
E
-
--
>70
50-70
<50
>70
40-70
<40
G
~
-
-
>10
5-10
<5
>15
5-15
<5
Reproductive Composition
10. Lithophilic spawning
species
E
-
-
-
>5
4-5
<4
>4
3-4
<3
G
-
-
-
>4
3-4
<3
>3
2-3
<2
Abundance and Health
11. Total catch per unit
effort
E
-
-
-
>100
60-100
<60
>120
60-120
<60
G
~
~
~
>25
15-25
<15
>20
10-20
<10
12. Percent individuals
with anomalies
E
--
--
-
<1
1-3
>3
<1
1-3
>3
G
-
-
-
<1
1-3
>3
<1
1-3
>3
* E = electrofishing; G = gill netting
-51-
-------
Table 3.4
1993 Vital Signs Monitoring
Benthic Macroinvertebrate Community Index of Biotic Integrity (IBI) metrics and scoring criteria developed for
Tennessee Valley Streams, with a score of 5 representing highest quality, and a score of 1 the poorest.
Stream Benthic Index of Biotic Integrity Metrics
Metric
Sampling
Gear
Score
1
3
5
Taxa Richness and Community Composition
1. Taxa Richness
Surber or Hess
<9
9-17
>.18
2. Occurrence of mollusk species"
Combined
0
--
_>1
3. Number of mayfly (Ephemeroptera) taxa
Surber or Hess
<3
3-5
>_6
4. Number of stonefly (Plecoptera) taxa
Surber or Hess
<2
--
_>_2
5. Number of caddisfly (Trichoptera) taxa
Surber or Hess
<2
2-3
>_4
6. Number of EPT taxa*
Combined
<14
14-24
>25
7. Proportion of oligochaetes
Surber or Hess
.>0.05
0.01-0.049
<0.01
8. Proportion of the two most abundant taxa
Surber or Hess
>.0.75
0.5-0.749
<0.5
Trophic and Functional-Feeding Group
9. Proportion as omnivores and scavangers
Surber or Hess
>0.9
0.6-0.89
<0.6
10. Proportion as collectors/filterers
Hess
J>0.5
0.2-0.49
<0.2
Surber
>0.6
0.3-0.59
<0.3
11. Proportion as predators
Surber or Hess
_<0.04
—
>0.04
Abundance
12. Total abundance in quantitative samples
(Lower scores given for extremely low and high values)
Combined
<.400
>5000
401-500
4001-5000
501-4000
* Metric applied to qualitative and quantitative samples combined. All other metrics
applied to individual quantitative samples and resultant scores averaged.
-52-
-------
Table 3.5
1993 Vital Signs Monitoring
Fish Community Index of Biotic Integrity (IBI) metrics and scoring criteria developed for Tennessee Valley Streams,
with a score of 5 representing highest quality, and a score of 1 the poorest.
Stream Fish Community Index of Biotic Integrity Metrics
Metric
Duck River 22.5
Bear Creek 25.2
Sequatchie River 7.1
Hiwassee River 37.0
1
3 5
I
3
5
1
3
5
1
3 5
Soecies Richness and Comoo.s
ition
1. Number of native
species
<27
27-53
>53
<23
23-44
>44
<23
23-45
>45
<21
21-41
>41
2. Number of darter
species
<5
5-9
>9
<4
4-7
>7
<5
5-8
>8
<5
5-8
>8
3. Sunfish species, less
Micronterus
<3
3-5
>5
<3
3-5
>5
<3
3-5
>5
<2
2-3
>3
4. Number of sucker
species
<4
4-7
>7
<4
4-7
>7
<4
4-7
>7
<4
4-7
>7
5. Number of intolerant
species
<4
4-6
>6
<2
2-3
>3
<3
3-4
>4
<2
2
>2
6. Percent tolerant
individuals
>20
10-20
<10
>20
10-20
<10
>20
10-20
<10
>20
10-20
<10
Troohic ComDOsition
7. Percent omnivores
>30
15-30
<15
>30
15-30
<15
>30
15-30
<15
>30
15-30
<15
8. Percent specialized
insectivores
<25
25-50
>50
<25
25-50
>50
<25
25-50
>50
<25
25-50
>50
9. Percent piscivores
<2
2-5
>5
<2
2-5
>5
<2
2-5
>5
<2
2-5
>5
Abundance and Healt
h
10. Catch rate*
<8
8-16
> 16
<8
8-16
>16
<8
8-16
>16
<8
8-16
>16
11. Percentage hybrids
>1
0-1
0
>1
0-1
0
>1
0-1
0
>1
0-1
0
12. Percent individuals
with anomalies
>5
2-5
>2
>5
2-5
>2
>5
2-5
>2
>5
2-5
>2
* Average number per seine haul or five minutes of boat electroshockine
-------
Table 3.5 (continued)
1993 Vital Signs Monitoring
Fish Community Index of Biotic Integrity (IBI) metrics and scoring criteria developed for Tennessee Valley Streams,
with a score of 5 representing highest quality, and a score of 1 the poorest.
Stream Fish Coi
nmunity Index of Biotic Integrity Metrics
Metric
Little Tenn River 94.3
Emory River 21.7
Powell River 65.4
Clinch River 172.3
1 3 5
1 3 5
13 5
1 3 5
Species Richness and Comnos
ition
1. Number of native
species
<11
11-20
>20
<15
15-29
>29
<21
21-39
>39
<22
22-42
>42
2. Number of darter
species
<3
3-4
>4
<5
5-8
>8
<5
5-8
>8
<5
5-8
>8
3. Sunfish species, less
Micropterus
0
1
>1
<2
2
>2
<2
2-3
>3
<2
2-3
>3
4. Number of sucker
species
<2
2-3
>3
<2
2
>2
<3
3-4
>4
<3
3-5
>5
5. Number of intolerant
species
<2
2
>2
<2
2
>2
<3
3-4
>4
<3
3-5
>5
6. Percent tolerant
individuals
>20
10-20
<10
>20
10-20
<10
>20
10-20
<10
>20
10-20
<10
TroDhic Comnosition
7. Percent omnivores
>30
15-30
<15
>30
15-30
<15
>30
15-30
<15
>30
15-30
<15
8. Percent specialized
insectivores
<25
25-50
>50
<25
25-50
>50
<25
25-50
>50
<25
25-50
>50
9. Percent piscivores
<2
2-5
>5
<2
2-5
>5
<2
2-5
>5
<2
2-5
>5
Abundance and Heal
h
10. Catch rate*
<7
7-13
>13
<7
7-13
>13
<8
8-16
>16
<8
8-16
>16
11. Percentage hybrids
>1
0-1
0
>1
0-1
0
>1
0-1
0
>1
0-1
0
12. Percent individuals
with anomalies
>5
2-5
>2
>5
2-5
>2
>5
2-5
>2
>5
2-5
>2
* Average number per seine haul or five minutes of boat electroshockins
-------
Table 3.5 (continued)
1993 Vital Signs Monitoring
Fish Community Index of Biotic Integrity (IBI) metrics and scoring criteria developed for Tennessee Valley Streams,
with a score of 5 representing highest quality, and a score of 1 the poorest.
Stream Fish Community Index of Biotic Integrity Metrics
Metric
Holston River 118.0
Nolichucky River 8.5
French Broad R 78.0
1
3 5
1 3 5
1
3 5
Soecies Richness and ComDosition
1. Number of native
species
<20
20-38
>38
<19
19-36
>36
<21
21-40
>40
2. Number of darter
species
<4
4-7
>7
<5
5-8
>8
<4
4-7
>7
3. Sunfish species, less
MicroDterus
<2
2-3
>3
<2
2-3
>3
<2
2-3
>3
4. Number of sucker
species
<3
3-5
>5
<4
4-6
>6
<4
4-6
>6
5. Number of intolerant
species
<3
3-4
>4
<2
2-3
>3
<2
2-3
>3
6. Percent tolerant
individuals
>20
10-20
<10
>20
10-20
<10
>20
10-20
<10
TroDhic ComDosition
7. Percent omnivores
>30
15-30
<15
>30
15-30
<15
>30
15-30
<15
8. Percent specialized
insectivores
<25
25-50
>50
<25
25-50
>50
<25
25-50
>50
9. Percent piscivores
<2
2-5
>5
<2
2-5
>5
<2
2-5
>5
Abundance and Heal
h
10. Catch rate*
<8
8-16
>16
<8
8-16
> 16
<7
7-13
>13
11. Percentage hybrids
>1
0-1
0
>1
0-1
0
>1
0-1
0
12. Percent individuals
with anomalies
>5
2-5
>2
>5
2-5
>2
>5
2-5
>2
* Average number per seine haul or five minutes of boat electroshocking
-------
Table 3.6
1993 Vital Signs Monitoring
Computational Method For Evaluation of Reservoir Health
Wilson Reservoir - 1993 (Run-of-the-river reservoir)
Aquatic Health Indicators
Observations
Ratings
Forebay
T rans i t i on
Zone
Inflow
Forebay
Transition
Zone
Inflow
Dissolved Oxygen:
Less Than 2 ma/L (Sumner Avg.)
X of X-Sectional Area
X of X-Sectional Bottom Length
Less Than 5 ma/I at 1.5m
Yes/No
11.0 (1)
44.2 (1)*
No
No Samples
Tail race DOs
Yes*
1
(poor)
*D0 was 1
*Mininn*n
No Rating
i mg/L on the
DO was 4.3 m
4
(fai r)
bottom
l/L
Chlorophyll-a, jig/L:
Summertime Average
Maximum Concentration
10.2
25.0
No Samples
No Samples
3
(fair)
No Rating
No Rating
Sediment Quality:
Toxicity
Ceriodaphnia Survival
Rotifer Survival
Chemistry
Metals/NH3/pesticides
T1 T2
100% 95%
65% 85%
None (5)
No Samples
No Samples
4.5
(good)
No Rating
No Rating
Benthic Conmunity:
Dominance
Tubificidae
Chi ronomidae
EPT
Long-lived
Taxa richness
Total
5
5
1
1
3
5
20
No Samples
5
5
5
5
5
5
30
3
(fair)
No Rating
5
(good)
Fish Community:
Electrofishing Score
Ci 11 Netting Score
Overall
46
38
42
No Samples
42
42
4
(fair)
No Rating
4
(fair)
Overall Reservoir Evaluation Key:
Less than 52% - poor (red)
52% to 72% - fair (yellow)
Greater than 72% - good (green)
Sampling Location Sum
15.5 of 25
--
13 of 15
Reservoir Sum
28.5 of 40 [71%]
OVERALL RESERVOIR EVALUATION
"fair" (yellow)
-------
Table 3.7
1993 Vital Signs Monitoring
Computational Method For Evaluation of Reservoir Health
Cherokee Reservoir - 1993 (Tributary storage reservoir)
Aquatic Health Indicators
Observations
Ratings
Forebay
Transition
Zone
Inflow
Forebay
Transition
Zone
Inflow
Dissolved Oxygen:
Less Than 2 mq/L (Summer Avg.)
% of X-Sectional Area
% of X-Sectional Bottom Length
Less Than 5 mq/l at 1.5m
Yes/No
21.5 (1)
43.0 (1)*
No
26.0 (1)
52.0 (1)*
No
No Samples
1
(poor)
*D0 was
1
(poor)
I mg/L on the
No Rating
bottom
Chlorophyl I-a, iig/L:
Summertime Average
Maximum Concentration
7.6
17.0
9.4
14.0
No Samples
5
(good)
5
(good)
No Rating
Sediment Quality:
Toxici tv
Ceriodaphnia Survival
Rotifer Survival
Chemistry
Metals/NH3/pest i ci des
100% (5)
90%
NH3 (3)
95% (1)
75%
Cu, NH3 (3)
No Samples
4
(fair)
2
(poor)
No Rating
Benthic Community:
Dominance
Tubificidae
Chironomidae
EPT
Long-Iived
Taxa richness
Total
3
3
1
3
1
5
16
No Samples
5
5
3
5
5
5
28
3
(fair)
No Rating
5
(good)
Fish Community:
Electrofishing Score
Gill Netting Score
OveralI
32
40
36
30
38
34
34
36
35
3
(fair)
3
(fair)
3
(fair)
Overall Reservoir Evaluation Key:
Less than 57% - poor (red)
>57% and <72% - fair (yellow)
Greater than 72% - good (green)
Sampling Location Sum
16 of 25
11 of 20
8 of 10
Reservoir Sum
35 of 55 [64%]
OVERALL RESERVOIR EVALUATION
"fair" (yellow)
-------
4.0 HYDROLOGIC OVERVIEW OF 1993
Many water quality characteristics (e.g., temperature, dissolved oxygen, conductivity,
water clarity, suspended solids, etc.) exhibit changes due to seasonal variations in atmospheric .
temperature and rainfall. During those times of the year when runoff is minimal (normally August-
October), streamflow is largely derived from the base flow of groundwater. Because of greater
contact between the water and the soil/rock and the longer groundwater residence times, groundwater
contains more dissolved minerals (i.e., higher concentrations of hardness and alkalinity, higher pHs
and conductivities, etc.) than does surface water. During those times of the year when runoff is
higher (normally January-March), streamflow is principally derived from rapid overland runoff that
allows little time for mineral dissolution.
Consequently, during those times of the year with higher rainfall and subsequent higher
flows, base flow accounts for a smaller proportion of the total streamflow, resulting in lower
concentrations of most dissolved constituents. In addition, periods of intense rainfall and high
overland flows wash off or "flush" a watershed and transport soil particles to streams, often carrying
large loads of nonpoint source pollutants (nutrients, suspended solids, fecal bacteria, etc.) to streams
and rivers.
In addition to flood control, electric power generation, and navigation, an important
benefit of the TVA's system of dams and reservoirs is its ability to maintain adequate streamflow
during extended periods of low rainfall and low runoff by the controlled release of water from
tributary storage impoundments. However, this alteration of natural streamflow (diminishing high
flows during floods and augmenting low flows during droughts) by storing and then slowly releasing
water from tributary storage impoundments creates conditions of strong thermal stratification and low
dissolved oxygen in the bottom waters of these tributary storage impoundments. (Additional details
about reservoir stratification and water quality impacts are discussed in Chapter 5.)
From a water quality perspective, the lower streamflows occurring during the warmer
summer months, combined with naturally occurring higher water temperatures and lower dissolved
oxygen concentrations, result not only in lakes becoming thermally stratified but also having less
water and less oxygen available to dilute and assimilate the wastes discharged to them. In addition,
the warmer water temperatures increase aquatic biological processes (respiration, bacteriological
decomposition, etc.). This results in oxygen being used at a faster rate, which can further lower
oxygen concentrations. In combination, these factors Oow streamflows and diminished assimilative
-59-
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capacity, warmer temperatures and higher biological oxygen consumption rates, and the inhibition of
mixing and reaeration caused by thermal stratification) result in low dissolved oxygen concentrations
and adversely impact the health of aquatic life. The summer of 1993 was a case in point. July 1993
was the hottest month on record (since 1890s) in the Tennessee Valley. Valley-wide temperatures
averaged almost 83 °F (28.3°C), about 5°F (2.8°C) above normal for July. For example, in
Chattanooga, all 31 days in July had temperatures above 90°F (32.2°C), with temperatures up to
104°F (40.0°C) and 15 days with temperatures 98°F (36.7°C) or higher. This record-breaking heat
(and low streamflows) resulted in high water temperatures in the Tennessee River. In fact, all nine
mainstem Tennessee River reservoirs had surface water temperatures that exceeded 86°F (30.0°C),
some with highs up to 90°F (32.2°C).
In addition, Tennessee Valley rainfall and runoff were well below normal in the summer of
1993. In July, Valley-wide rainfall averaged only 1.76 inches (45 mm), a deficit of 3 inches (76 mm)
below the long-term July mean of 4.77 inches (121 mm) as a result rainfall runoff was only 0.66
inches (17 mm), compared to the long-term July mean of 1.03 inches (26 mm). Further, runoff was
significantly lower in the western half of the Tennessee Valley than in the eastern half. In July,
runoff above Chattanooga was 90 percent of the long-term mean, while runoff was only 64 percent of
the long-term mean above Kentucky Dam. For the period of January through July, runoff above
Chattanooga was 80 percent of the long-term mean, while runoff was 72 percent of the long-term
mean above Kentucky Dam. Consequently, flows in the Tennessee River in 1993 increasingly fell
below the long-term average as the river flowed downstream from Fort Loudoun Dam to Kentucky
Dam.
The high temperatures and low flows of July 1993 adversely impacted dissolved oxygen
concentrations in the Tennessee River, particularly in the downstream reservoirs. In mid-July,
hypolimnetic anoxia (DOs equal to 0 mg/L) was found in the forebays of Kentucky, Pickwick,
Wilson, Wheeler, and Chickamauga Reservoirs. All time low concentrations of DO were recorded in
the releases from Chickamauga Dam on July 16 (2.2 mg/L) and Nickajack Dam on July 19
(1.8 mg/L) when flows from both dams were only 9000 eft. During the first two weeks of July (July
1 to 15), daily flows averaged only about 17,250-17,500 eft at Chickamauga and Nickajack Dams, or
about 55 percent of the normal flow for this period of time. Once the effects of the high temperatures
and low flows on DOs in the Tennessee River were recognized, flows were immediately increased (by
drawing water from tributary storage reservoirs) and DO concentrations improved. For example, at
Chickamauga Dam, from July 16-31, average daily flows were increased to an average of about
-60-
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24,500 cfs (about 80 percent of the normal flow for July) and DOs in the releases increased to an
average of about 4.3 mg/L, ranging from 3.2 to 6.3 mg/L. Compounding this whole situation were
the record-setting rains and flooding occurring in the mid-West along the Mississippi and Missouri
Rivers during the "flood of the century." During this period, TVA minimized discharge from the
Tennessee River through Kentucky Dam so as to not increase flood crests on the lower Ohio and
Mississippi Rivers and worsen the already catastrophic flooding in those areas.
Obviously, examining atmospheric temperature, rainfall, and runoff patterns during 1993
aids in interpretation of the Vital Signs monitoring data and the ecological health assessments of the
streams and reservoirs. Interestingly, interpretation of the biological components of stream
monitoring results for 1993 is not influenced by these extreme hydrologic conditions. The low
rainfall and low streamflows during the spring and early summer allowed benthic sample collection
before the more stressed conditions developed in mid-to-late summer.
4.1 Atmospheric Temperature
Average annual temperature in the TVA region is approximately 60 degrees Fahrenheit, °F
(15.6 degrees Celsius,°C), with January usually being the coldest month and July the hottest.
According to U.S. Department of Commerce (USDOC) climatic data, atmospheric temperatures in the
TVA region averaged only about 0.3°F (0.2°C) warmer than normal in 1993; however, 1993 was a
year of extremes (USDOC, 1993). January and July were unusually warm with 5.0°F (2.8°C) and
4.7°F (2.6°C) above normal, respectively; while, March and April were below normal with
departures greater than -2.0°F (-1.1 °C) (Figure 4.1a).
In review, 1993 began with an unusually warm January but cooled to below normal in
February. As has often occurred in the last 15 years, another cold spring with late freezes was
experienced. A record-breaking late season blizzard struck the Valley in mid-March and hit hardest
in the eastern half. Summer was hotter than normal, with Tennessee, Alabama, Georgia, North
Carolina, and Virginia all having the hottest July on record since the 1890s. The persistent heat and
high humidity created great stress on livestock and people. The daily records for Chattanooga
Airport provide an indication of the unusual conditions. All 31 days had maximums above 90°F
(32.2°C), with the observed maximums ranging from 92°F (33.3°C) to 104°F (40°C) and 15 days of
98°F (36.7°C) or higher. The last four months had near or below normal temperatures, and the
annual average temperature was only slightly above normal.
-61-
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4.2 Rainfall
The Tennessee River basin averages about 51-52 inches (1295-1320 millimeters [mm]) of
precipitation annually. However, there are large variations in the spatial distribution of precipitation.
The range is from a high of about 93 inches (2360 mm) in the mountains of southwestern North
Carolina near Highlands, North Carolina, to a low of about 37 inches (940 mm) in the shielded
valleys of these same mountains near Asheville, North Carolina. Elsewhere in the Valley,
precipitation usually ranges within five to ten inches (127 mm to 254 mm) of the basin average.
March is usually the wettest month and October the driest.
Rainfall across the Tennessee Valley in 1993 averaged only 39.8 inches (1011 mm),
almost 12 inches (about 300 mm) or 23 percent less than the long-term 100-year average. The
diminished rainfall in 1993 followed another dry year, 1992, when annual rainfall was about 8 inches
(204 mm) or about 15 percent below the long-term average. The period January-May 1992 ranked as
one of the ten driest on record in the Tennessee Valley. During 1993, only the month of December
had rainfall greater than normal (6.1 inches [155 mm] compared to normal December rainfall of 4.8
inches [122 mm]); the greatest rainfall deficit occurred in July (1.8 inches [45 mm] compared to the
normal July rainfall of 4.8 inches [122mm]). In addition to the extremes of December and July,
March and September precipitation was close to average while February, April, June and October
were more than an inch (254 mm) below average (Figure 4.1b). During March 1993, the Tennessee
Valley received the equivalent of 5.4 inches (137 mm) of rain, much of this during the "Winter Snow
Storm of the Century" when many areas received record amounts (greater than 20 inches [about 500
mm]) of snowfall.
The unusually persistent hot weather and below average rainfall in the summer was related
to an unusual upper air pattern, which kept the storm track well west and north of the region and
allowed very few cold fronts to reach the Tennessee Valley. This nearly stationary position of a
strong upper air trough over the Rocky Mountains was associated with the record flooding in the
middle of the country and kept the Southeast hot and dry. This general pattern was most persistent in
the summer, but frequently alternated with a pattern having an upper trough over or to the east of the
Valley in the other seasons. This latter trough kept most storms associated with it to the south of the
TVA region. These two upper air patterns dominated the weather during 1993, so significant rainfall
events tended to occur only when there was a transition period between one and the other.
-62-
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4.3 Streamflow
Streamflow varies seasonally with rainfall, although during the spring and summer
evaporation and transpiration also significantly reduce the amount of runoff. Watersheds that receive
50 to 60 inches (1270 to 1524 mm) of precipitation annually average about 20 to 30 inches (508 to
762 mm) of runoff. In a normal year, the discharge of the Tennessee River (approximately 66,000
cfs [1868 meters'/second]) corresponds to about 22 inches (about 560 mm) of runoff distributed over
the 40,900 square mile (105,930 square kilometer) drainage basin. A larger amount of runoff occurs
during the wet winter and spring months (January-April) when precipitation events are frequent,
temperatures are low, and there are no leaves on deciduous vegetation. Consequently, soil
absorption, evaporation, and plant transpiration losses are low at that time of year, and both runoff
and streamflow are higher than during the summer and autumn months. Average rainfall in the
eastern and western portions of the Tennessee Valley (above and below Chattanooga) is about equal.
However, topographic differences (viz. the largely steep and mountainous terrain in the eastern
portion of the Valley, compared with the mostly flat and rolling terrain in the western portion of the
Valley) and generally shallower soils result in higher amounts of runoff above Chattanooga.
In 1993, runoff for the Tennessee River basin was well below normal, particularly from
February through July and particularly in the western half of the Valley. Runoff above Chattanooga
was only slightly below normal in 1993, 21.4 inches, or 92 percent of the long-term mean of 23.4
inches. However, runoff above Kentucky Dam was only 17.6 inches, a deficit of almost 5 inches and
only 78 percent of the long-term mean of 22.5 inches (Figure 4.1c.). Table 4.1 shows that the 1993
releases from tributary reservoirs in the western part of the Valley (e.g., Normandy, Tims Ford, etc.)
were below their long-term means, while the releases from tributary reservoirs in the eastern part of
the Valley (e.g., South Holston, Watauga, etc.) were close to normal. Consequently, flows in the
Tennessee River in 1993 increasingly fell below the long-term average as the river flowed
downstream from Fort Loudoun Dam to Kentucky Dam.
Figure 4.2 presents the relative contributions of streamflow based on long term averages
from major tributaries and local inflows to each of the mainstem Tennessee River reservoirs. The
flow through each mainstem reservoir is dominated by the inflow from the immediately adjacent
upstream reservoir. However, several large tributaries (e.g., Hiwassee River, Elk River, Duck
River) do provide substantial inputs to a few mainstem reservoirs, and consequently can have a
significant impact on water quality, depending on the volume and chemical quality of the inflows.
-63-
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FIGURE 4.1 Temperature, Precipitation, and Runoff - Tennessee River Basin, 1993
5
Jan Feb Mar Apr May Jun Jul Aug Sept Oct Nov Dec 1993
FIGURE 4 1a Temperature Departures From Long—Term Mean (deg F) in the TVA Region
Jan Feb Mar Apr May Jun Jul Aug Sept Oct Nov Dec 1993
FIGURE 4.1b FYecipitotion Departures From Long-Term Mean (Inches)
For The Tennessee River Basin
Jan Feb Mar Apr May Jun Jul Aug Sept Oct Nov Dec 1993
FIGURE 4 lc Runoff Departures From Long-Term Mean (inches)
For Tennessee River Basia. Above Kentucky Oam
-64-
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Figure 4.2 Average Annual Tennessee River Flows Showing Contributions of Major
Tributaries and Local Inflows.
v.v :-M ^'aViV/WiVm
¦illB
IIIII!
i;;::: mi Mm
mi 111 n m iiu m
• r y f'.rr i s | • i |
^WIIUIItlH!
[ I I
Fort Loudoun Watts Bar Chickamauga Nickajack
Guntersville Wheeler
Wilson
Pickwick Kentucky
-------
Table 4.1
CHARACTERISTICS OF VITAL SIGNS RESERVOIRS
Average
Average
Average
Hydraulic
CY 1993
Drainage
Reservoir
Surface
Depth
Annual
Reservoir
Residence
Reservoir
Reservoir
Area
Length"
Area"
at Dam'
Volume"
Drawdownb
Flow-POR
Time-1993"
Flow
Name
(sa. miles)
f miles)
(acres)
(ac-ft)
_£ftL
(cfs)
(davs)
(cfs)
1000's
1000's
Run-of-the-River Reservoirs
Kentucky
40,200
184.3
160.3
88
2,839
5
66,600
27.5
52,097
Pickwick
32,820
52.7
43.1
84
924
6
54,900
9.6
48,566
Wilson
30,750
15.5
15.5
108
634
3
51,500
6.8
47,236
Wheeler
29,590
74.1
67.1
66
1,050
6
49,400
11.4
46,264
Guntersville
24,450
75.7
67.9
65
1,018
2
40,700
12.9
39,691
Nickajack
21,870
46.3
10.4
60
241
0
35,900
3.6
34,092
Chickamauga
20,790
58.9
35.4
83
628
7
34,200
9.6
32,887
Watts Bar
17,300
72.0/24.0°
39.0
105
1,010
6
27,100
19.5
26,145
Fort Loudoun
9,550
50.0
14.6
94
363
6
18,400
9.7
18,897
Melton Hill
3,343
44.0
5.7
69
120
0
4,920
12.7
4,764
Tellico
2,627
33.2
16.5
80
415
6
6,300d
34.0
6,159d
Tributary, Storage Reservoirs
Norris
2,912
73.0/53.0C
34.2
202
2,040
32
4,190
249.4
4,124
Cherokee
3,428
54.0
30.3
163
1,481
28
4,460
162.2
4,604
Douglas
4,541
43.1
30.4
127
1,408
48
6,780
109.4
6,490
Ft Patrick Henry
1,903
10.4
0.9
81
27
0
2,650
5.6
2,423
Boone
1,840
17.4/15.3C
4.3
129
189
25
2,550
38.5
2,477
South Holston
703
23.7
7.6
239
658
33
976
341.3
972
Watauga
468
16.3
6.4
274
569
26
714
403.5
711
Fontana
1,571
29.0
10.6
460
1,420
64
3,840
173.5
4,126
Hiwassee
968
22.2
6.1
255
422
45
2,020
98.8
2,154
Chatuge
189
13.0
7.0
124
234
10
459
291.3
405
Nottely
214
20.2
4.2
167
170
24
416
228.0
376
Ocoee #1 (Parksville)
595
7.5
1.9
115
85
7
1,420
33.1
1,296
Blue Ridge
232
11.0
3.3
156
193
36
614
156.2
623
Tims Ford
529
34.2
10.6
143
530
12
940
328.7
813
Bear Creek
232
16.0
0.7
74
10
lle
380
14.4
337
Cedar Creek
179
9.0
4.2
79
94
14e
282
185.7
255
Little Bear Creek
61
7.1
1.6
82
45
12°
101
253.9
90
Beech
16
5.3
0.9
32
11
1°
14
616.2
9
Normandy
195
17.0
3.2
83
110
11
320
201.7
275
* Measurements based on normal maximum pool.
b Tennessee River and Reservoir System Operation and Planning Review, Final EIS, TVA/RDG/EQS-91/I, 1990.
c Major/minor arms of reservoir.
d Estimated flow based on releases from Chilhowee Dam (POR avg. = 4770cfs), and adjusted based on the additional drainage area between
Chilhowee Dam (1977 sq miles) and Tellico Dam (2627 sq miles).
e Estimated based on difference between normal maximum summer pool and average minimum winter pool elevations.
-------
5.0 DISCUSSION
The quality of water in a river system is a result of the quality of water flowing into it
from many sources (e.g., tributary streams, discharges from metropolitan areas, overland runoff) and
the internal physical, chemical, and biological processes which occur within the river. The water
quality of major tributaries to a river is governed by geologic characteristics, rainfall, and human
activities within the watershed.
The Tennessee River originates with the confluence of the French Broad and Holston
Rivers at Knoxville, Tennessee. It receives water from a variety of tributaries reflecting the
geochemical characteristics of the watersheds they drain. For example, the French Broad and Holston
Rivers are nutrient-rich and moderately hard, with greater hardness in the Holston; the Little
Tennessee and Hiwassee Rivers are soft and nutrient-poor; the Clinch River is hard with moderate
nutrients; while the other two large tributaries, the Elk and Duck Rivers, are relatively hard and
nutrient-rich.
Each tributary exerts its influence based on a wide variety of factors, but primarily the
volume of inflow and concentrations of various chemical constituents. Nutrient levels are particularly
important because of their direct influences on algal primary production and indirect influences on
dissolved oxygen.
Just as the characteristics of the Tennessee River are a composite of its major tributaries,
each major tributary has characteristics of its tributaries. Given the widely varying geochemical
attributes and many different types of land use within a watershed, characteristics of streams and
reservoirs vary greatly among major tributary watersheds. These characteristics are further
influenced by the location, design, and operation of dams on streams in the watershed.
This report summarizes results and conclusions from 1993 monitoring activities in the
Tennessee Valley. This chapter (Chapter 5) examines these results from a Valley-wide perspective.
Chapters 6-17 present a watershed-by-watershed perspective for each of 12 delineated drainages that
together comprise the Tennessee Valley. Volume II of this report is a detailed summary of the 1993
monitoring results in each of these 12 watershed areas.
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5.1 Vita] Signs Monitoring
5.1.1 Reservoirs
Reservoirs were divided into two categories for comparative purposes: run-of-the-river
reservoirs (the nine mainstream reservoirs plus the two navigable tributary reservoirs) and the 19
tributary storage reservoirs. The primary differences between these two categories are retention time
and changes in pool level due to winter drawdown; both have a great effect on the aquatic ecosystem.
For comparative purposes, all reservoirs were categorized as good, fair, or poor based on their
respective ecological health evaluations.
Run-Of-The-River Reservoirs—The ecological health of all 11 run-of-the-river reservoirs
rated fair or better in 1993. The score for Fort Loudoun Reservoir (58 percent) was the lowest of the
run-of-the-river reservoirs. This score fell just within the fair range; but low enough to be considered
poor-fair. Three reservoirs rated fair - Tellico (63 percent), Watts Bar (68 percent) and Melton Hill
(68 percent); four rated good - Nickajack (88 percent), Chickamauga (83 percent), Guntersville (78
percent), and Kentucky (75 percent); and the remaining three reservoirs fell close to the break point
used to separate good and fair reservoirs (>72 percent) - Pickwick (73 percent), Wheeler (72
percent), and Wilson (71 percent).
Figure 5.1 shows an interesting geographical trend to these results. Reservoirs with the
lowest scores were at the upstream end of the Tennessee River, followed by reservoirs with the
highest scores, and then reservoirs with intermediate scores in the downstream portion of the
Tennessee River. There are many factors which in combination result in the observed ecological
conditions, and care must be taken not to oversimplify complex ecosystem dynamics. However, one
obvious consideration would be the nutrient rich waters from the French Broad and Holston Rivers,
coupled with high human population densities in east Tennessee. Together, these create a high
potential for undesirable ecological conditions to exist in the upper Tennessee River. Inputs of fairly
pristine waters from the Little Tennessee River, further supplemented by inflows from Hiwassee
River with low nutrients further downstream, act to dilute the water in the Tennessee River and help
diminish the potential for eutrophic conditions in Chickamauga, Nickajack, and Guntersville
Reservoirs. In the lower half of the Tennessee River, water naturally rich in nutrients flows from the
Elk River to Wheeler Reservoir and from the Duck River to Kentucky Reservoir, stimulating algal
growth and potentially shifting ecological conditions toward a more productive state.
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The four reservoirs with the lowest ecological health scores (Fort Loudoun, Tellico,
Melton Hill, and Watts Bar) had multiple indicators that rated poor or very poor. These were
generally dissolved oxygen, sediment, benthos, and/or fish assemblage. For the three reservoirs
which scored good (Chickamauga, Nickajack, and Guntersville), all ecological health indicators rated
fair or better, except for dissolved oxygen at the inflows to Nickajack and Guntersville Reservoirs.
Scores for the next four reservoirs which scored fair to good (Wheeler, Wilson, Pickwick, and
Kentucky) varied greatly depending upon the number and location of sample sites within the
reservoir. Indicator ratings at sample sites on the Tennessee River portion of each reservoir (i.e., the
main body of the reservoir) were fair or better, except for dissolved oxygen at the Wheeler and
Wilson forebays. Sample sites in major embayments generally had several indicators with poor or
very poor ratings.
Embayments were not monitored prior to 1993. Four of the largest embayments in the
Tennessee Valley were included in 1993 monitoring activities-Big Sandy River embayment on
Kentucky Reservoir, Bear Creek embayment on Pickwick Reservoir, Elk River embayment on
Wheeler Reservoir, and Hiwassee River embayment on Chickamauga Reservoir. All four
embayments have surface areas of about 5000 acres (about 2000 hectares) or greater and local
drainage areas greater than 500 square miles (1295 km2). Water quality characteristics within an
embayment and the resulting ecological health conditions are largely controlled by factors within the
embayment's immediate watershed and the rate of water exchange between the embayment and the
main body of the reservoir. The Hiwassee and Elk River embayments have substantial flow through
them. The Big Sandy and Bear Creek embayments have much smaller inflows and less water
exchange with the main body of the reservoir.
Results from the Hiwassee River and Elk River embayment sites substantiate the above
discussion of the potential for inflows from these rivers to affect conditions in the Tennessee River.
All five ecological indicators rated good or excellent in the Hiwassee embayment. Three ecological
health indicators were poor or very poor, one fair and one good in the Elk River embayment.
Inclusion of monitoring results from embayments had a substantial effect on reservoir
health ratings for three of the reservoirs compared to previous years. For example, Kentucky
Reservoir rated good (75 percent) in 1993, lower than the 1992 rating, when Kentucky had the best
rating (88 percent) of all reservoirs examined. The primary factor responsible for this decrease was
addition of the sample site in Big Sandy River embayment. If results from the Big Sandy River
embayment were excluded from the overall reservoir score, the revised rating (83 percent) would be
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similar to that observed for 1992. Pickwick Reservoir had an ecological health rating of 73 percent
for 1993. However, if the Bear Creek embayment information were deleted, the reservoir score
would be 80 percent. A similar situation is true for Wheeler. The overall health rating for Wheeler
would change from 72 percent to 82 percent if results from the Elk River embayment were excluded.
Interestingly, the overall ecological health score for Chickamauga Reservoir would change little if
results from the site in Hiwassee River embayment were excluded (i.e., 83 percent with and 81
percent without).
Another factor which lowered ecological health scores in the run-of-the-river reservoirs in
1993 was relatively low dissolved oxygen during summer 1993. Extreme summer weather in 1993
caused record high water temperatures and low DO in much of the Tennessee River. Special dam
operations and water releases to reduce impacts from these conditions were started as soon as the low
DO conditions were detected. Special monitoring showed these releases improved DO concentrations.
However, DO concentrations were lower than in previous years causing lower scores for the overall
health rating. (See Chapter 4, Hydrologic Overview of 1993, for additional detail.)
The ecological health score for one other reservoir (Tellico) changed substantially from
previous years. The rating was 63 percent (fair) for 1993 compared to 48 percent in 1992 and 44
percent in 1991 (both poor). The primary causes of the higher score were better ratings for DO at
the forebay (mostly the result of an improved, more accurate method of calculating the score for this
indicator) and addition of information from the transition zone collection site which was relocated in
1993. The change in DO scoring resulted in forebay DO being rated fair in 1993; it had previously
been rated poor. Two indicators, chlorophyll and DO, received excellent ratings at the new transition
zone site; and the other three indicators rated poor. The higher ecological health score for 1993 is
considered to be more representative of the true environmental conditions in Tellico Reservoir than
scores in previous years.
Tributary Reservoirs—Monitoring on tributary reservoirs was not fully implemented until
1993. The number of tributary reservoirs included in Vital Signs monitoring expanded from three in
1990 to 19 in 1993. Also, the number of ecological health indicators expanded in 1993 when
sediment quality and benthic macroinvertebrates were sampled for the first time on tributary
reservoirs. Sample design for tributary reservoirs specifies less intensive monitoring for water
chemistry constituents (most notably nutrients) than on the run-of-the-river reservoirs because of the
more static nature of water within tributary reservoirs. Monitoring efforts for other ecological
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indicators (chlorophyll, sediment, benthos, and fish) were the same on both run-of-the-river and
tributary reservoirs for the first time in 1993.
The ecological health evaluations for the tributary reservoirs are more tentative than for the
run-of-the-river reservoirs. The data base generally is quite small, and our understanding of how to
weigh and integrate results from various ecological health indicators is still in development.
A problem associated with evaluating the ecological health of tributary reservoirs is the
individuality of each reservoir. There is substantial variation in physical characteristics (depth,
shoreline development, area, length), reservoir operations (retention time, drawdown, depth of
outflow, etc.), watershed geochemistry, and land use. This individuality makes it difficult to establish
reference or expected conditions, against which to rate the observed ecological characteristics as
good, fair, or poor ecological health. (See Section 3.1 for additional discussion.)
Two attributes, long retention times and deep drawdowns, of tributary reservoirs
particularly are significant. Long retention times create high potential for thermal and chemical
stratification. As solar wanning occurs in upper strata during spring and summer, bottom strata
remain cold, and thermal stratification develops. If oxygen demand is sufficient, which is the
typically the case, anoxia occurs in the bottom waters. Under these conditions, iron and manganese
become more soluble, and their concentrations increase. If anoxia continues long enough, high levels
of ammonia and sulfide also can develop. These conditions cause stresses to aquatic life and result in
low ecological health ratings.
Deep drawdowns of the pool during winter, sometimes below the elevation of the summer
thermocline, also have a pronounced effect on aquatic systems of tributary reservoirs. For example:
(1) stable shoreline habitats cannot develop or persist; (2) benthic substrates in upper riverine reaches
of the reservoir can be covered with sand and silt when the reservoir is full but be washed to gravel
or bedrock when the area returns to a riverine environment at winter, low pool elevations; and (3)
spring spawning sites can be left dry or covered with many feet of water depending upon dam
operations during spring filling. Again, these have undesirable ecological effects.
Considering these factors, the ecological health of tributary reservoirs is not expected to be
as good as run-of-the-river reservoirs. Results for 1993 support this expectation. No tributary
reservoir rated good for ecological health, and only two rated fair-to-good. Both Fort Patrick Henry
Reservoir and Blue Ridge Reservoir scored 72 percent, just at the break point used to indicate good
or fair ecological health conditions. Interestingly, Fort Patrick Henry, even though a tributary
reservoir, has retention time and drawdown characteristics like a run-of-the-river reservoir. Blue
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Ridge Reservoir has quite low primary productivity, which, coupled with essentially a full depth
withdrawal from the dam, helps prevent dissolved oxygen problems.
Only one tributary reservoir rated poor. Parksville (Ocoee No. 1) Reservoir scored 52
percent with poor scores for four of the five indicators. Dissolved oxygen had an excellent rating.
This is contrary to expectations for a tributary reservoir, but this reservoir represents an unusual case.
A very low oxygen demand exists in the hypolimnion due to very low primary productivity rates.
The reservoir is recovering from years of pollution problems related to copper mining and industrial
activities at Copperhill. A more thorough discussion of Parksville Reservoir is provided in Section
12.5. Two reservoirs (Normandy and Cedar) scored 56 percent, right at the break point between
poor and fair. Dissolved oxygen was the primary problem in both cases. Of the remaining 14
reservoirs, eight rated near the middle of the fair range and six rated in the fair range just above poor
(Figure 5.2).
Figure 5.2 indicates there were no geographical patterns associated with overall reservoir
scores. No particular watershed had mostly high scoring or low scoring reservoirs. Also, physical
characteristics such as size or depth seemed to have little influence on reservoir score.
The ecological health indicator which was most often associated with low ecological health
scores was DO. As discussed above, this was expected. Poor or very poor DO scores occurred at
one or more sample sites in 13 of the 19 tributary reservoirs sampled. All six tributary reservoirs in
the middle and western part of the Tennessee Valley were in this group, along with seven of the 13
tributary reservoirs in the eastern, mountainous area of the Valley. The six reservoirs in the middle
and western end of the Valley (Tims Ford, Normandy, Bear Creek, Little Bear Creek, Cedar Creek,
and Beech Creek) exhibit strong thermal stratification, generally have high chlorophyll concentrations,
and have substantial agriculture activities in their watersheds. The seven in the eastern end of the
Valley vary greatly in a number of characteristics. Of these, four (Norris, Douglas, Cherokee, and
Nottely Reservoirs) had all or mostly very poor DO ratings, followed by South Holston with one very
poor rating and Boone and Fontana with only one poor rating and no very poor ratings.
Of the six reservoirs with fair, good, or excellent DO scores, two were in the Holston
watershed (Fort Patrick Henry and Watauga), and four were in the Hiwassee watershed (Hiwassee,
Chatuge, Blue Ridge, and Parksville). All except Fort Patrick Henry had relatively low nutrient and
chlorophyll concentrations (most with seasonal chlorophyll averages below 3.0 fig/L). Although Fort
Patrick Henry had high chlorophyll values, lack of stratification and short retention time helped
maintain good DO concentrations.
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In most cases, reservoirs with poor DO concentrations would be expected to have poor
benthic macroinvertebrate communities. This was true for seven of the 13 reservoirs with DO
problems. Interestingly, the remaining six reservoirs with poor DO had fair, good, or even excellent
benthos scores. Norris and Cherokee Reservoirs in east Tennessee and Little Bear Creek, Cedar
Creek, and Beech Creek Reservoirs in the western end of the Valley had very poor DO scores, yet
fair benthic macroinvertebrate communities. Bear Creek, also in the western end of the Valley, had a
very poor DO score yet an excellent benthos score. These results and their potential implications are
difficult to interpret with only one year of benthic macroinvertebrate data available. Additional
monitoring results should help clarify these results. An initial interpretation is that the benthic
community is able to recover quickly between autumn reoxygenation of bottom sediments and sample
collection the following spring. Another possibility is that some of the samples collected along the
transect were above the oxygen-stressed stratum. Results from individual samples suggest both
factors may have contributed to the observed ratings.
Just as reservoirs with poor DO ratings typically would be expected to have poor benthos,
reservoirs with good DO levels would be expected to have a good benthos community, unless some
other factor was negatively influencing the benthos. This was the case on Watauga, Hiwassee, and
Parksville Reservoirs. All had fair to excellent DO scores yet all had poor or very poor benthic
macroinvertebrate communities. Poor scores for Parksville Reservoir were not surprising, given the
problems that reservoir has experienced over the years from upstream mining activities. Results for
the other two reservoirs were unexpected. Acute toxicity to at least one test animal was observed in
all three reservoirs. More detailed assessment efforts would be required to determine whether there is
a real relationship between the apparent toxicity and poor benthic communities. Results from
additional monitoring in 1994 will be examined closely to determine whether more detailed
assessments should be planned.
5.1.2 Streams
Twelve of the major Tennessee River tributaries were included in Vital Signs Stream
Monitoring in 1993 (Table 2.2). Six additional streams will be monitored beginning in 1994.
Results for 1993 showed a wide range of ecological conditions among the 12 streams.
Three, Clinch, Powell, and Little Tennessee Rivers, had the highest possible scores for all four
ecological health indicators (nutrients, sediment, benthic macroinvertebrates, and fish community).
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The lowest score (50 percent) was for the French Broad River where nutrients and fish rated poor,
benthos rated fair, and sediments rated good.
Scores for the remaining eight streams were evenly distributed within this range. The
Emory and Hiwassee Rivers had good overall scores (90 and 88 percent, respectively) with fair
ratings for benthos, the only indicator rating less than the maximum score at each stream. The
Nolichucky and Sequatchie Rivers also rated good with scores of 80 percent each. At both streams,
two indicators rated good and two fair. Three streams rated fair (Duck River-70 percent, Bear
Creek-70 percent, and Holston River-68 percent). High nutrient concentrations on the Duck and
Holston Rivers caused a poor rating for nutrients; the other three indicators rated fair or good. The
lower score for Bear Creek was due to most indicators rating fair, rather than due to any indicator
rating poor. Ratings for the remaining stream, Elk River, must be used conservatively because only
three indicators were monitored in 1993. The fish community was not sampled in 1993. The overall
score for the other indicators was 60 percent; nutrients rated poor, benthos fair, and sediment good.
The fish community will be sampled in 1994.
The ecological health indicator that rated poor most often was nutrients. Four streams
(Duck, Elk, Holston, and French Broad Rivers) received poor ratings for nutrients. Bear Creek and
the Nolichucky River received a fair rating for nutrients and the remaining six streams rated good.
All of these results were expected based on individual watershed characteristics.
5.2 Use Suitability Monitoring
5.2.1 Bacteriological Studies
Fifty-nine designated swimming beaches, 12 informal swimming areas, and 14 canoe
launching or landing sites were sampled in 1993. All of the designated swimming beaches and
informal swimming areas and eight of the canoe access sites met the regulatory criterion of having
geometric mean concentrations of fecal coliform bacteria less than 200/100 mL if rainfall samples
were excluded. Two swimming beaches, one each on Tims Ford and Watts Bar Reservoirs, and the
canoe site sampled on the Elk River, slightly exceeded the criterion when rainfall samples were
included. The four access sites on the Duck River exceeded the geometric mean criterion for both
rainfall and nonrainfall samples.
Thirty-five nonrecreation sites were also sampled to provide generic bacteriological water
quality data on Wilson, Guntersville, Nickajack, Fort Loudoun, Norris, Douglas, Cherokee,
Fort Patrick Henry, Boone, South Holston, and Watauga Reservoirs; four sites were sampled on the
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Duck, Clinch, and South Holston Rivers; and three sites on Spring, Beidleman, and Thomas Creeks.
All but one reservoir site (Nickajack) and two stream sites (Beidleman and Thomas Creeks) met
recreation criteria.
A comparison of the results of this survey with surveys in 1974, 1986, and 1989 through
1992 shows bacteria concentrations in 1974 and 1993 were similar, and lower than during the other
years. The differences are probably caused by different weather conditions and sampling methods
rather than reflecting long-term changes in bacteriological water quality.
Fecal coliform samples were taken in conjunction with Vital Signs monitoring activities on
the 11 run-of-the-river reservoirs from April through September 1993. Fifteen of the 155 samples
analyzed had concentrations greater than the normal detection limit of 10/100 mL, seven exceeded
100/100 mL. No location had more than one sample exceed 100/100 mL.
The results of studies summarized above are consistent with previous surveys. Fecal
coliform concentrations were generally lower in 1993 due to lower than normal summer rainfall.
Bacteriological water quality in most areas of TV A reservoirs is good. In streams it is much poorer,
especially after rainfall.
5.2.2 Fish Tissue Studies
Availability of results for fish tissue studies is usually delayed because of the intricate
laboratory procedures required to analyze fish tissue samples. This process usually takes several
months; so results for samples collected in autumn usually are not available until the next spring.
Results in this report are for fish collected during summer and autumn 1992. Additional fish were
collected in summer and autumn 1993 but results were not available in time to be included in this
report.
Screening Studies—Results of screening studies in 1992 did not indicate any new reservoirs
or streams in need of intensive investigations. Two streams and six reservoirs had at least one analyte
slightly elevated indicating a need to resample in autumn 1993 at the screening level. Streams
included the Emory River (PCB concentration in channel catfish 1.1 fig/g) and the Holston River
(mercury concentration in largemouth bass 0.57 uglg). Reservoirs included Pickwick (DDTr
2.5 figlg), Bear Creek (mercury 0.45 uglg), Little Bear Creek (mercury 0.56 uglg), Norris
(PCBs 0.9 figlg), Fontana (PCBs 1.1 uglg and mercury 0.53 uglg), and Cherokee (PCBs 0.8 uglg).
Although most reservoirs had multiple sites sampled, an elevated concentration of an analyte at any
site would cause that reservoir to be included in this list.
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All sites listed above were resampled in autumn 1993 for the same fish species. In
addition, because several tributary reservoirs had somewhat elevated mercury concentrations, efforts
in autumn 1993 were directed at better evaluating this condition by analyzing both channel catfish, the
species typically used as the indicator, and largemouth bass, a top predator which would be expected
to have higher mercury concentrations than catfish.
Intensive Studies—Six TVA reservoirs (Wheeler, Nickajack, Watts Bar, Fort Loudoun,
Melton Hill, and Parksville) were examined intensively in 1992. Intensive studies are conducted on
reservoirs where a contaminant problem is known or suspected. PCBs was the contaminant of
interest on all these reservoirs, except Wheeler, where DDTr (total DDT) is the problem. Chlordane
was also of interest in some of these reservoirs. Fish consumption advisories which recommend
either limiting the quantity of fish eaten or avoiding any consumption are in effect for all six
reservoirs except Parksville. These advisories issued by the Tennessee Department of Environment
and Conservation and by the Alabama Department of Public Health are based in part on the results of
these studies.
Results from autumn 1992 collections indicated somewhat lower concentrations of DDTr in
fish from Wheeler Reservoir and PCBs in fish from Nickajack Reservoir. Lower concentrations in
one year should not be interpreted as a significant decrease in contaminant concentration. Previous
results have shown substantial year-to-year variability. The long-term study on Watts Bar Reservoir
identified substantially lower PCB concentrations in 1989 and 1990 than in previous years.
Subsequent results for 1991 and 1992 returned to the higher concentrations of previous years. For
this reason, comparable studies were repeated on these reservoirs in autumn 1993.
Results of 1992 fish tissue samples from Watts Bar, Fort Loudoun, and Melton Hill
Reservoirs generally fell within the range observed in previous years. Likewise, limited results for
Tellico Reservoir fell within historical ranges.
Screening studies on Parksville (Ocoee No. 1) Reservoir over the past several years have
found PCB concentrations near the level used by the state of Tennessee to issue a "Limit
Consumption" advisory. As a result, TVA and the state designed and conducted a more detailed
sampling of fish from there in autumn 1992. Results of the 1992 effort confirmed previous results of
relatively high PCB concentrations in channel catfish - the average of ten fish was 1.5 /zg/g at the
forebay and 1.0 fig/g at an upper reservoir location. Largemouth bass were also examined and found
to have lower concentrations than catfish-averages at the two sites were 0.6 and 0.7 jig/g,
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respectively. Bluegill sunfish and rainbow trout composites from these areas had low concentrations.
There had been no action taken on these results at the time this report was prepared.
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Figure 5.1 Overall Ecological Health of Run-of-the-River Reservoirs in the Tennessee Valley in
1993. (Ecological Health Indicators are shown as a proportion of their contribution to the overall score for each reservoir.)
Kentucky
Pickwick
I I
Wilson Wheeler
Ountersville
Nickajack
Chickamauga Watts Bar Fort Loudoun Melton Hill
Tellico
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Figure 5.2 Overall Ecological Health of Tributary Reservoirs in the Tennessee Valley in 1993.
(Ecological Health Indicators are shown as a proportion of their contribution to the overall score for each reservoir.)
Nofris
Beech Normandy
I I I I I I
Douglas Cherokee Fort Patrick Boone South Watauga Fontana Hiwassee Chatuge Ocoee #1 Nottely Blue Tims Bear Little Bear Cedar
Henry Holston Ridge Ford Creek Creek Creek
Beech Reservoir score is based on four rather than five indicators; indicator and overall scores are shown on the same scale as other
reservoirs to facilitate comparisons.
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6.0 KENTUCKY RESERVOIR WATERSHED
The Kentucky Reservoir watershed area includes all streams flowing into the Tennessee
River downstream of Pickwick Landing Dam at Tennessee River mile (TRM) 206.7 to the confluence
of the Tennessee River with the Ohio River. The one exception is the Duck River which is
considered a separate watershed. The Kentucky Reservoir watershed area is relatively large (4590
square miles) and has an average annual discharge of about 66,600 cfs. Of that, about 82 percent
(54,000 cfs) comes into Kentucky Reservoir from Pickwick Landing Dam. The Duck River supplies
about 6 percent (4075 cfs), with the remaining 11 percent coming from local inflows.
Kentucky Reservoir is the dominant feature of this watershed. There are four monitoring
sites on Kentucky Reservoir—forebay, transition zone, inflow, and Big Sandy River embayment
(Figure 6.1 and Table 2.1). Information from 1993 monitoring activities on Kentucky Reservoir is
provided in Section 6.1.
The watershed also includes the seven small reservoirs on the Beech River. The largest,
Beech Reservoir, is the only one included in Vital Signs monitoring. Given its small size, the forebay
is the only site monitored (Figure 6.1). Monitoring information for Beech Reservoir for 1993 is in
Section 6.2.
There were no stream monitoring sites in this watershed in 1993. Beginning in 1994, a
site will be established on the Clarks River for monitoring biological conditions.
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Figure 6,1 Map of the Kentucky
Reservoir Watershed Showing
Reservoir Monitoring Sites in
1993.
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6.1 Kentucky Reservoir
Physical Description
Kentucky Reservoir is the largest reservoir on the Tennessee River. The dam is located at
Tennessee River Mile (TRM) 22.4, and the reservoir extends 184 miles upstream to Pickwick Dam at
TRM 206.7. At full pool the surface area is 160,300 acres, and the shoreline is 2280 miles.
Average annual discharge is about 66,600 cfs, which provides an average hydraulic retention time of
about 22 days. Additional information about Kentucky Reservoir is provided in Table 4.1.
The Duck River, a major tributary to the Tennessee River (and Kentucky Reservoir),
provides about 6 percent of the total flow through Kentucky Reservoir. The confluence of the Duck
River with the Tennessee River is at TRM 110.7.
The transition zone sample location was moved prior to the 1992 sample season from
TRM 112.0 to TRM 85.0. Results for 1990 and 1991 at TRM 112.0 indicated that location was
more representative of a riverine environment than a transition environment. The 1992 and 1993
results indicate the new transition zone site is correctly located.
Vital Signs monitoring was expanded in 1993 to include a sample site in four of the largest
embayments in the Tennessee Valley. One, the Big Sandy River embayment on Kentucky Reservoir,
is the largest embayment in the Tennessee Valley. It covers 15,238 surface acres and has over 93
miles of shoreline. Because its watershed is only 629 square miles, there is very little water
exchange.
Ecological Health
The ecological health of Kentucky Reservoir rated good (75 percent) in 1993. This is
lower than the ecological health index for 1992, when Kentucky had the best rating (88 percent) of all
reservoirs examined. It is also lower than the overall rating in 1991. Primary factors responsible for
this decrease were lower dissolved oxygen (DO) concentrations due to the hot, dry summer of 1993,
and the addition of a sample site in Big Sandy River embayment. If results for the sample site in Big
Sandy embayment were excluded from calculating the overall reservoir score, the revised rating (83
percent) would be similar to that observed for 1992.
The transition zone was the best of the four sites examined in 1993. All ecological health
indicators (DO, chlorophyll-a, sediment quality, benthos, and fish) rated good or excellent at that site.
The site in the Big Sandy embayment approached the other extreme. Three indicators rated poor or
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very poor: chlorophyll because of high concentrations, sediment quality because of high ammonia
and toxicity to test organisms, and fish assemblage because of low fish abundance and species
richness. No indicators at the other two sites (forebay and inflow) rated poor or very poor.
Aquatic plants covered about 3465 acres in 1993 compared to about 2600 acres in 1992
and 2800 in 1991. Most plants were found around islands and shallow embayments downstream of
the Duck River.
Reservoir Use Suitability
Use Suitability monitoring activities did not identify any impairments on Kentucky
Reservoir in 1993. Twenty-four recreation sites have been sampled for fecal coliform bacteria one or
more times on Kentucky Reservoir since 1989. None has exceeded the geometric mean criteria for
recreation. In 1992 three sites exceeded one of EPA's recommended guidelines-more than 10
percent of the samples had fecal coliform concentrations greater than 400/100 mL. In 1993 these
three sites were resampled, and all met the EPA guideline. Fecal coliform bacteria concentrations
have been very low at the Vital Signs locations sampled since 1990.
Examination of channel catfish fillets in autumn 1992 from six locations between Kentucky
and Pickwick Dams found only low levels of heavy metals and pesticides at all locations. The only
analyte high enough to be of interest was lead at 0.6 figlg at one location in 1992. Similar
concentrations have been found sporadically in previous years, but there has been no pattern in space
or time.
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6.2 Beech Reservoir
Physical Description
Beech Reservoir, the largest of seven small flood control projects on the Beech River
system in western Tennessee, is formed by Beech Dam at Beech River mile 35.0. Beech Reservoir is
only 5.3 miles long and averages only about 12 feet deep. It has no hydropower generating facilities,
but is the primary source of water for the city of Lexington. The reservoir is an urban lake with
considerable residential lakefront development. Consequently, it receives a large amount of
recreational use relative to its small size (about 900 acres). Discharge from Beech Dam averages
only about 14 cfs per day, resulting in a long hydraulic residence times of 300 to 400 days.
Reservoir Health
During 1991 and 1992 only water quality monitoring was conducted in Beech Reservoir.
The 1991 and 1992 data indicated poor ecological health in Beech Reservoir, as evidenced by very
low concentrations of dissolved oxygen and high chlorophyll-a concentrations.
In 1993 four of the five ecological health indicators (algae, dissolved oxygen, sediment
quality, and benthos) were sampled on Beech Reservoir. Overall, the ecological health rated fair (65
percent). Chlorophyll rated excellent (at the upper end of the mesotrophic range), below observed
concentrations during 1991 and 1992. As expected, DO rated very poor. Sediment quality rated
good and benthic macroinvertebrates rated fair. The fish assemblage will be added to the sampling
regime in 1994.
Reservoir Use Suitability
No bacteriological studies were conducted in 1993. Fecal coliform concentrations were
low at the swimming beach in 1990. There are no fish consumption advisories on Beech Reservoir.
Fish tissue samples have not been collected by TVA from this reservoir.
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7.0 DUCK RIVER WATERSHED
The Duck River Watershed includes all streams flowing into the Duck River. It has an
area of 3500 square miles and an average annual discharge of 4075 cfs to Kentucky Reservoir on the
Tennessee River. The Duck River basin is underlain almost entirely by limestone, or phosphatic
limestone; consequently, waters in the streams draining this basin are fairly hard and contain large
concentrations of minerals. Large deposits of phosphate ores permit phosphate mining and refining
operations in the basin. Phosphate concentrations in surface and groundwater are significantly higher
than in most of the Tennessee Valley. The soils are thin with limestone outcrops at the surface in
many places, and sinkholes are common throughout the watershed.
Normandy Reservoir is the only reservoir in this watershed. This is a relatively small
reservoir and only the forebay is included in the Vital Signs monitoring program (Figure 7.1).
There is one stream monitoring site on the Duck River at mile 26.0 (Figure 7.1).
Information from monitoring activities on Normandy Reservoir and the Duck River are in
Sections 7.1 and 7.2, respectively.
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Duck River
I
00
00
1
/
Figure 7.1 Map of the Duck River Watershed
Showing Stream and Reservoir Monitoring
Sites in 1993.
A Stream Monitoring Sites
• Reservoir Monitoring Sites
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7.1 Normandy Reservoir
Physical Description
Normandy Reservoir is formed by Normandy Dam at Duck River mile (DRM) 248.6.
Normandy Reservoir, constructed primarily for flood control and water supply, has a drainage area of
195 square miles and no electric power generation capacity. One of TVA's smaller reservoirs,
Normandy at lull pool elevation has about 3200 surface acres, 73 miles of shoreline, and about
17 miles of impounded backwater. The reservoir has an average depth of about 35 feet and an
average annual drawdown of about 11 feet. The average annual discharge from Normandy Dam is
about 320 cfs, providing an average annual retention time of about 175 days.
Ecological Health
The ecological health of Normandy Reservoir rated poor-fair (56 percent) in 1993. Vital
Signs monitoring previously had not been conducted on this reservoir, although several special studies
had been completed. As expected, DO conditions were among the poorest observed on any Vital
Signs reservoir in 1993. DO rated very poor because anoxia existed, 77 percent of the cross-sectional
bottom length had DO concentrations <2.0 mg/L, and 48 percent of the cross-sectional area had DO
levels <2.0 mg/L. Sediment quality rated poor due to high levels of ammonia and toxicity to test
animals. Benthic macroinvertebrates also rated very poor, likely due to such poor bottom conditions.
Based on past studies, there was concern about very high levels of primary productivity in
Normandy Reservoir. Sampling in 1993 did not find this to be the case. Chlorophyll rated good at
the forebay sample location because the annual average chlorophyll concentration was within the
mesotrophic range, and no single sample had a very high chlorophyll concentration.
The other indicator, fish assemblage, rated excellent. Normandy Reservoir had one of the
best fish assemblages examined on tributary reservoirs in 1993. Most of the 12 metrics received the
highest possible score.
Reservoir Use Suitability
Fecal coliform samples were collected at two swimming beaches and three boat ramps in
1992. While concentrations were low at the boat ramps, several samples were high at each of the
beaches, although the geometric means were well within recreation criteria. The two beaches were
sampled again in 1993. Fecal coliform concentrations were much higher, but the geometric means
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were still within criteria. Local geese populations are the probable source of the high bacteria
concentrations.
There are no fish consumption advisories on Normandy Reservoir. A composite sample of
channel catfish collected from the forebay in autumn 1992 was screened for pesticides, PCBs, and
selected metals. All analytes were either not detected or found in only low concentrations.
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7.2 Duck River Stream Monitoring Site
Physical Description
The Duck River flows westward from its headwaters in northwestern Coffee County,
Tennessee, for more than 280 miles through the Nashville basin and Highland Rim physiographic
provinces in middle Tennessee to meet the Tennessee River. The basin is approximately 125 miles
long and 30 miles wide and drains 3500 square miles.
The stream monitoring location is at the USGS stream gage above Hurricane Mills,
Tennessee. The Duck River basin above Hurricane Mills is 2557 square miles or 73 percent of the
entire Duck River basin. Principal tributaries in the monitored area include the Piney River (223
square miles), Big Swan Creek (155 square miles), Lick Creek (101 square miles), and Big Bigby
Creek (129 square miles) which drain the Highland Rim province; and Rutherford Creek (116 square
miles), Fountain Creek (103 square miles), Big Rock Creek (121 square miles), and Garrison Fork
(130 square miles) which drain the Nashville Basin. Normandy Dam forms the only major
impoundment located on the upstream reach of the Duck River stream monitoring site.
A principal tributary that flows into the Duck River below the stream monitoring location
is the Buffalo River that drains 764 square miles (22 percent of the Duck River basin). The Buffalo
River basin lies entirely within the Highland Rim province and the streams generally contain low
concentrations of dissolved minerals.
Ecological Health
The stream monitoring site on the Duck River showed generally fair ecological health in
1993, similar to 1992. This was driven by high phosphorus concentrations and fair conditions for the
fish community. Sediment quality and the benthic macroinvertebrate community both rated good, an
improvement over 1992 observations. Undesirable conditions at this site included extensive bank
erosion and unstable bottom substrate conditions. Although the Duck contributes only about 6.5
percent of the total flow of Kentucky Reservoir under average flow conditions, it can contribute
significant amounts of nutrients and sediment to the reservoir.
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Use Suitability
A reach of the Duck River from 3.5 to 7.1 miles downstream of Normandy Dam was
found to greatly exceed bacteriological criteria for water contact recreation in 1993, probably due to
dairies.
All metal and organic analytes in fish tissue samples were not detected or found in low
concentration.
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8.0 PICKWICK RESERVOIR - WILSON RESERVOIR WATERSHED
Pickwick Reservoir and Wilson Reservoir on the Tennessee River are the most notable
features of this drainage area. Only a small part of the flow leaving this watershed actually originates
within the watershed itself. The average annual discharge from Pickwick Dam is 54,900 cfs. Of
that, 49,500 cfs (90 percent) is the discharge from Wheeler Dam into Wilson Reservoir. About 2100
cfs enters Wilson Reservoir through local tributaries and about 3400 cfs originates in tributaries to
Pickwick Reservoir. The streams within this watershed drain an area of about 3230 square miles.
The largest tributaries are Bear Creek, a tributary to Pickwick Reservoir with a drainage area of about
945 square miles, and Shoal Creek, a tributary to Wilson Reservoir, with a drainage area of about
445 square miles.
Four small reservoirs were built on Bear Creek in the late 1970s and early 1980s for flood
control and recreation. These are Bear Creek, Little Bear Creek, Cedar Creek, and Upper Bear
Creek Reservoirs.
Reservoir monitoring activities occur at the forebay, transition zone, and inflow on
Pickwick Reservoir and at the forebay and inflow on Wilson Reservoir (Figure 8.1). Wilson is
relatively short and has no definable transition zone. Because of their smaller size, only the forebays
of Bear Creek, Little Bear Creek, and Cedar Creek Reservoirs are monitored. No monitoring
activities are conducted on Upper Bear Creek because of TVA's program to destratify and oxygenate
water in the forebay.
The only stream monitoring site is on Bear Creek at Bear Creek mile 27.3. Results for
1993 reservoir and stream monitoring activities within this watershed are provided in the following
sections:
8.1 Pickwick Reservoir
8.2 Wilson Reservoir
8.3 Bear Creek Reservoir
8.4 Little Bear Creek Reservoir
8.5 Cedar Creek Reservoir
8.6 Bear Creek Stream Monitoring Site
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8.1 Pickwick Reservoir
Physical Description
Pickwick Reservoir is immediately upstream of Kentucky Reservoir on the Tennessee
River. Pickwick Dam is located at TRM 206.7. Like the rest of the mainstream, run-of-the-river
reservoirs, Pickwick is much shorter (53 miles long) and smaller (43,100 acres and shoreline of 496
miles) than Kentucky Reservoir. Average annual discharge is about 55,000 cfs, which provides an
average hydraulic retention time of about eight days. Additional information about reservoir
characteristics is in Table 4.1.
A major tributary, Bear Creek, joins the Tennessee River in Pickwick Reservoir at about
mile 225. Bear Creek provides, on the average, about 2.5 percent of the flow through Pickwick
Reservoir.
Reservoir Monitoring activities were expanded on Pickwick Reservoir in 1993 to include a
Vital Signs monitoring site in Bear Creek embayment. This rather large embayment (7200 acres)
extends from the mouth of Bear Creek upstream about 17 miles to the point where flow is not
affected by backwater from Pickwick Dam.
Ecological Health
The ecological health of Pickwick Reservoir was fair to good in 1993 (73 percent), similar
to 1992 and 1991. All ecological health indicators rated between fair and excellent at all locations,
except chlorophyll, which rated very poor (indicating high algal productivity) at the new sample site
in Bear Creek embayment. There was a general decline in DO conditions throughout the reservoir in
1993 with DO rated fair to good at all locations. In 1992 DO was good to excellent at all locations.
Summer 1993 was characterized by low rainfall, low flows, and high temperatures, hence lower DO
concentrations were expected.
Conditions at the transition zone improved in 1993 for chlorophyll and sediment quality.
Sediments contained lower mercury concentrations than in previous years; however, concentrations
were still slightly above background. Although chlorophyll concentrations were in the fair range in
1993 (because of relatively high average concentrations), this was an improvement over 1992 when
concentrations were even higher.
Benthic macro invertebrates at the inflow location, downstream of Wilson Dam, were
improved in 1993, rating excellent as compared to fair in 1992 and poor in 1991. The improvement
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between 1991 and 1992 was partly due to an improved evaluation system and partly due to actual
improvements in the health of the community of bottom animals. The 1993 results indicate continued
improvements in the benthos.
At the forebay, the fish assemblage evaluation has shown substantial variation from year to
year. The rating was good in 1991, poor in 1992 (very few fish collected), and good in 1993.
Interestingly, a low number of fish were collected from this location by electrofishing in 1993, yet an
abundance of fish were collected by gill netting. The 1992 rating was based only on electrofishing
results, whereas the 1993 rating was based on results from both techniques. Overall, there appeared
to be little change in the fish assemblage among years.
The new sample site in Bear Creek embayment had one very poor indicator (chlorophyll-
too high), three fair indicators (DO-zero on bottom; sediment-toxicity to test organisms; benthos-
mostly tolerant organisms present), and one good indicator (fish). Of the four sites sampled on
Pickwick Reservoir in 1993, the Bear Creek embayment site had the poorest ecological health. If
results for this site were deleted from calculating the overall reservoir score, the reservoir score
would be 80 percent.
There were only about 105 acres of aquatic plants on Pickwick Reservoir in 1993, similar
to the 100 acres in 1992.
Reservoir Use Suitability
Use Suitability monitoring did not identify bacteriological nor fish tissue contamination
problems. There are no fish consumption advisories on Pickwick Reservoir based on fish collected
from 1988 through 1992. Concentrations of metals, PCBs, and pesticides in composited catfish fillets
were relatively low except for total DDT concentrations in the fall 1992 inflow sample. Given the
rare occurrence of elevated total DDT concentrations in fish from Pickwick, it is likely that one of the
catfish in the composite came from Wheeler Reservoir, which has a significant, localized DDT
contamination problem. Fecal coliform bacteria concentrations were low at ten swimming areas
sampled in 1993. Bacteria concentrations at the Vital Signs locations sampled since 1990 have been
low.
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8.2 Wilson Reservoir
Physical Description
Wilson Reservoir is quite different from other mainstream Tennessee River reservoirs in
both length and depth. Wilson Dam is located at TRM 259.4 and Wheeler Dam is at TRM 274.9,
providing a length of only 15.5 miles, a shoreline of 154 miles, and surface area of 15,500 acres.
Water depth in the forebay is slightly over 100 feet. This short, deep pool, coupled with the largest
hydroelectric generating plant in the TVA system, provides for short hydraulic retention times (six
days). Average annual discharge from Wilson is 51,500 cfs. Because of the physical characteristics,
design, and operation of Wilson Dam (primarily upper strata withdrawal for hydropower generation),
low DO conditions develop in deeper strata of the forebay during summer months.
Ecological Health
Ecological health of Wilson Reservoir improved somewhat in 1993 compared to 1992 and
1991. Overall, Wilson Reservoir rated fair to good (71 percent) in 1993 compared to 60-70 percent
in previous years. One of the persistent problems in Wilson Reservoir is low concentrations of
dissolved oxygen (< 1 mg/L) in the forebay during summer months. The problem was more severe
in summer 1993 due to the drought conditions (high temperatures, low rainfall, and low flows).
Anoxia developed near the bottom, and a large proportion of the bottom and water column had DO
concentrations <2.0 mg/L, leading to a very poor rating.
A massive algal bloom caused extremely high chlorophyll concentrations at the forebay in
1992 resulting in a poor rating that year. Chlorophyll concentrations were lower in 1993, but still
relatively high and, therefore, rated fair in 1993. The benthic macroinvertebrate community at the
forebay rated better in 1993 (fair) compared to previous years (consistently poor). Poor ratings had
been attributed to the low concentrations of DO near bottom during summer. Given that benthos
collections were made in March 1993, prior to the severe DO problems later that summer, these
samples would have been more representative of 1992 conditions. Even though DO concentrations in
summer 1992 were not good, they were the best documented on Wilson since the Vital Signs
monitoring program began in 1990. The duration of low DO concentrations was relatively short in
1992 and the proportion of bottom with low DO concentrations was small. These conditions may
have provided sufficient opportunity for recolonization of several benthic species resulting in the
improved community rating for 1993. Samples to be collected in March 1994 will help determine
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whether this hypothesis is correct. If correct, the benthos rating for 1994 should be poor because of
the severe DO conditions in summer 1993.
Sediment quality at the forebay was good in 1992 and 1993, indicating no impairment due
to bottom substrates. This was an improvement over 1991 when fair sediment quality conditions were
found due to lower survival rates for test organisms. All ecological health indicators measured at the
inflow location (DO, fish, and benthos) were good or excellent in 1993.
There were only 54 acres of aquatic plants on Wilson Reservoir in 1993.
Reservoir Use Suitability
There are no fish consumption advisories on Wilson Reservoir based on fish tissue studies
conducted over the past several years.
Fecal coliform bacteria concentrations were very low at the two boat ramps tested in 1993
and at the Vital Signs location in the forebay. The low rainfall in 1993 may have contributed to low
concentrations at the boat ramps. All fecal coliform samples collected in the forebay since 1990 have
been low.
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8.3 Bear Creek Reservoir
Physical Description
With a surface of only 700 acres, Bear Creek is one of the smallest reservoirs in the TVA
system. It is relatively long (16 miles), narrow, and deep (74 feet at the dam). The average annual
discharge is 380 cfs providing an average hydraulic retention time of about 13 days. Average annual
drawdown is about 11 feet. Bear Creek Reservoir stratifies in the summer and develops hypolimnetic
anoxia. Another water quality concern is abandoned strip mines in the watershed.
Ecological Health
The ecological health of Bear Creek Reservoir rated fair (60 percent) in 1993. Vital Signs
monitoring previously had not been conducted on this reservoir. This reservoir appears to have a
high rate of primary productivity and significant hypolimnetic DO depletion. Summer chlorophyll
concentrations were higher on Bear Creek Reservoir than on any of the other tributary reservoirs
monitored in 1993. Only one of the five indicators (benthic macroinvertebrates) rated excellent and
one rated good (fish). Such high ratings would not be expected given the very poor rating for DO
(anoxia and large proportion of the water column with low DO concentrations) and poor rating for
sediment quality (high ammonia and toxicity to test animals). Continued monitoring in future years
will help to better define the ecological health of Bear Creek Reservoir.
Use Suitability
Fecal coliform bacteria concentrations were low at both of the swimming areas surveyed in
1993. The low rainfall in 1993 may have contributed to low concentrations. During a wetter period
in 1991, fecal coliform concentrations were higher, but still well within water quality criteria for
recreation. A single composite of channel catfish was collected from the forebay in autumn 1992.
All metal and organic analytes were low or not detected, except for mercury which was high enough
to warrant reexamination in autumn 1993 but not high enough to indicate a need for an in-depth,
intensive study.
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8.4 Little Bear Creek Reservoir
Physical Description
Little Bear Creek Reservoir is relatively short (7.1 miles long) and deep (84 feet at the
dam). It has a surface area of 1600 acres. With an average annual discharge of 101 cfs, the
hydraulic retention time is 225 days. Compared to Bear Creek Reservoir, the lower flow into the
reservoir and larger reservoir volume make the retention time much longer in Little Bear Creek
Reservoir. Average annual drawdown is about 12 feet.
Ecological Health
Little Bear Creek Reservoir had a fair (64 percent) ecological health rating in 1993. This
was the first year for Vital Signs monitoring on Little Bear Creek Reservoir. Similar to the other
reservoirs in the Bear Creek watershed, the most obvious problem was very poor DO conditions at
the forebay. Other indicators rated good (chlorophyll and fish assemblage) or fair (sediment quality
and benthos). Given the hot, dry summer of 1993, additional information in future years will help to
better evaluate and define the ecological health of Little Bear Creek Reservoir.
Reservoir Use Suitability
Fecal coliform bacteria concentrations were very low at both swimming areas tested in
1993. The low rainfall in 1993 may have contributed to low concentrations. During a wetter period
in 1991, fecal coliform concentrations were much higher at both beaches. During the 1991 survey
period, bacteriological water quality at both sites was within state water quality criteria for recreation;
however, both exceeded one of EPA's recommended guidelines—more than 10 percent of the samples
had fecal coliform concentrations greater than 400/100 mL.
A composite of channel catfish was collected from the forebay of Little Bear Creek
Reservoir in autumn 1992. Only one metal analyte (mercury) was detected, and no PCB or pesticide
analytes were detected. The mercury concentration (0.56 /xg/g) was relatively high. As a result,
channel catfish from this site were reexamined in autumn 1993. Results were not available at the
time this report was prepared.
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8.5 Cedar Creek Reservoir
Physical Description
Like the other reservoirs in the Bear Creek watershed, Cedar Creek Reservoir is small
(only nine miles long and 4200 acres surface area) and deep (79 feet at the dam). The low average
annual discharge from the dam (282 cfs) creates a relatively long average retention time (168 days).
This combination of physical features lead to thermal stratification and hypolimnetic anoxia in the
summer. Average annual drawdown is about 14 feet.
Ecological Health
The ecological health of Cedar Creek Reservoir rated poor-fair (56 percent) in 1993, the
first year of Vital Signs monitoring. As expected based on the other reservoirs in the Bear Creek
watershed, DO rated very poor because of anoxic conditions and a very large proportion of both the
bottom and the water column with DO concentrations <2.0 mg/L. Chlorophyll, benthos, and fish
assemblage all rated fair. The only fair to good rating was for sediment quality. There were no
excellent ratings.
Reservoir Use Suitability
Fecal coliform bacteria concentrations were low at the Slickrock Ford swimming area in
1993. The low rainfall in 1993 may have contributed to low concentrations. During a previous
survey period in 1991 with more normal rainfall, higher fecal coliform concentrations were found.
Despite being higher, they were within state water quality criteria for recreation.
A single composite of channel catfish fillets collected from the forebay of Cedar Creek
Reservoir in autumn 1992 did not have detectable concentrations of any pesticide or PCB analyte.
Mercury, found at a low concentration, was the only metal analyte detected.
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8.6 Bear Creek Stream Monitoring Site
Physical Description
Bear Creek flows through the southwest boundary of the Highland Rim physiographic
province in northwestern Alabama (85 percent) and northeastern Mississippi to join the Tennessee
River as an embayment of Pickwick Reservoir. The Bear Creek watershed is approximately 65 miles
long and 15 miles wide and drains 946 square miles.
The watershed area above the Bishop, Alabama, monitoring location is 667 square miles or
70 percent of the entire Bear Creek basin. Within the monitored area, Cedar Creek, with a drainage
area of 329 square miles, is the principal tributary. There are four reservoirs (Cedar Creek, Little
Bear Creek, Bear Creek, and Upper Bear Creek) that control the runoff from about half of the
watershed.
The Bear Creek basin is underlain by sandstone or has limestone outcroppings.
Approximately 70 percent of the watershed is forested, the remainder agricultural. Some iron ore has
been mined in the basin and bacterial pollution from agricultural operations has been recognized as a
water quality concern. Several active and abandoned coal mines are located on the uppermost
portions of the watershed above the upper Bear Creek Reservoir. Russellville and Haleyville,
Alabama, are the primary urban areas.
Ecological Health
The monitoring location on Bear Creek, far upstream of any influence of impoundment
from Pickwick Reservoir, showed fair ecological health in 1993. The fish community was fair in
1993; but not as good as in 1992, which was much improved over past years. Benthic
macroinvertebrates also rated fair in 1993, similar to 1992.
Use Suitability
The only bacteriological samples collected from the Bear Creek watershed in 1993 were
those collected for reservoir Vital Signs monitoring and are reported with those sections.
Fish for tissue analysis are not collected from the Bear Creek stream monitoring site.
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9.0 WHEELER RESERVOIR - ELK RIVER WATERSHED
The Wheeler Reservoir - Elk River watershed drains about 5140 square miles in north
central Alabama and south central Tennessee. Wheeler Reservoir is the fourth of nine reservoirs on
the Tennessee River. About 24,500 square miles of the Tennessee Valley are upstream of this
watershed. Wheeler Reservoir receives an average annual inflow of 40,700 cfs from Guntersville
Dam. Discharges from Wheeler Dam average 49,400 cfs on an annual basis leaving 8700 cfs which
originate within the watershed.
The largest tributary to Wheeler Reservoir is the Elk River, which has a drainage area of
about 2250 square miles and contributes about 3000 cfs. The remaining flow enters from tributaries
directly to Wheeler Reservoir.
Wheeler Reservoir is the largest reservoir within this watershed followed by Tims Ford
Reservoir on the Elk River. There are four Vital Signs monitoring sites on Wheeler Reservoir-
forebay, transition zone, inflow, and the Elk River embayment (Figure 9.1 and Table 2.1). Two sites
are monitored for Vital Signs on Tims Ford Reservoir-forebay and mid-reservoir. Woods Reservoir
on the Elk River is not included in this monitoring program because it is property of the Arnold
Engineering Development Center, Arnold Air Force Base.
The only stream monitoring site within this watershed is on the Elk River at mile 36.5.
Results from 1993 monitoring activities are provided in Section 9.1 for Wheeler Reservoir,
Section 9.2 for Tims Ford Reservoir, and Section 9.3 for the stream site on the Elk River.
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0
00
1
Elk River
^ Wheeler
Reservoir
TN
AL
Figure 9.1 Map of Wheeler
Reservoir - Elk River
Watershed Showing Stream
and Reservoir Monitoring
Sites in 1993.
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9.1 Wheeler Reservoir
Physical Description
Wheeler Reservoir has the third-largest surface area (67,100 acres) of all reservoirs in the
TVA system. It is 74 miles long (dam at TRM 274.9) and has 1063 miles of shoreline. Average
annual discharge is about 49,400 cfs which provides an average hydraulic retention time of about 11
days. Information collected in 1990 and 1991 indicated a more riverine than transition environment
at TRM 307.5; consequently, in 1992 the transition zone sampling location was relocated further
downstream to TRM 295.9. Results for 1992 and 1993 are being evaluated to determine if this new
site is suitably located or if it needs to be moved further downstream.
The Elk River joins the Tennessee River in the downstream portion of Wheeler Reservoir
at about mile 284 and provides, on the average, about 6 percent of the flow through Wheeler
Reservoir.
Vital Signs monitoring activities were expanded in 1993 to include a site in the Elk River
embayment. This was one of four embayments added to the Vital Signs program in 1993. The Elk
River embayment covers about 4900 acres. Given the relatively high flows in the Elk River (about
3000 cfs annual average), there is substantial water exchange in this embayment.
Reservoir Health
Like several other Tennessee River reservoirs, the overall ecological health index of
Wheeler Reservoir was lower in 1993 compared to 1992 and 1991. Overall, Wheeler Reservoir rated
fair to good (72 percent) in 1993 compared to good in 1992 (80 percent) and in 1991 (87 percent).
The primary contributor to this lower reservoir rating was addition of information from the Elk River
embayment, which had three poor ratings (chlorophyll-very poor; DO and benthos-poor). Of the
four sites monitored on Wheeler Reservoir in 1993, the Elk River embayment site had the poorest
ecological health. If data from the Elk River site were deleted from the overall score, Wheeler would
rate good (82 percent), consistent with findings in 1991 and 1992.
DOs less than 2 mg/L were measured at lower depths in the forebay during summer with
an anoxic area near bottom. As a result, DO rated poor at the forebay. (Ratings for DO at the
forebay had been good in 1991 and fair in 1992.) This stressed condition was likely related to the
low flows during the 1993 summer. Interestingly, DO rated excellent at the inflow and transition
zone, indicating the problem developed within the downstream, forebay region of the reservoir.
When low reservoir flows and high water temperatures occur, respiration and oxygen demand
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(both sediment and biological) increase and can exceed the DO made available by reaeration and
photosynthesis. This downstream portion of Wheeler Reservoir usually has relatively high algal
productivity due to input of high levels of phosphorus from Elk River. The combination of stagnant
water and a high oxygen demand required to decompose dead algae settling to the bottom contributes
to low DOs in lower depths at the forebay. All other ecological health indicators rated fair, good, or
excellent, similar to previous years. The transition zone and inflow had mostly good or excellent
rating for all indicators. The fish assemblage and sediment quality were fair, good, or excellent at all
sample sites.
Aquatic macrophytes colonized about 6600 acres on Wheeler Reservoir in 1993, compared
to about 4400 acres in 1992 and 3500 acres in 1991.
Reservoir Use Suitability
No bacteriological studies were conducted at recreation sites in Wheeler Reservoir in 1993.
In 1990, bacteriological water quality met the Alabama criterion for recreation at the four swimming
beaches and four boat ramps tested. Fecal coliform bacteria concentrations have generally been low
at the Vital Signs locations in the forebay and transition zones. Since 1990, only two samples have
been high, one in 1990 and one in 1993, both in the transition zone.
The Alabama Department of Public Health advises that most fish species from within the
Indian Creek embayment on Wheeler Reservoir should not be eaten due to DDT contamination. An
intensive study was conducted in autumn 1991 to determine if high concentrations existed in fish from
the Tennessee River in an area IS miles downstream to five miles upstream of the Indian Creek
embayment. Based on the 1991 results the public was further advised not to eat largemouth bass,
channel catfish, and smallmouth buffalo from within one mile either side of the area where Indian
Creek and the Tennessee River join. Other bottom feeding fish species (such as carp and suckers)
from the area should also be avoided. Furthermore, channel catfish caught from the Tennessee River
between Indian Creek and the Interstate 65 bridge should not be eaten. Fish were again collected
from these areas in the Tennessee River in 1992 to continue examining DDT concentrations. The
1992 fish had much lower concentrations than those in 1991. The study was reported in autumn
1993, but results were not available at the time this report was prepared.
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9.3 Elk River Stream Monitoring Site
Physical Description
The Elk River flows for more than 200 miles from its headwaters near Monteagle,
Tennessee, on the edge of the Cumberland plateau, southwest through south-central Tennessee into
northern Alabama where it meets the Tennessee River about nine miles above Wheeler Dam. The
basin, which lies principally in the Highland Rim province, is approximately 100 miles long and 50
miles wide at its greatest width, but it averages only 25 miles wide. Approximately one-third of the
north central basin above the Elk River lies in the Nashville basin. The Elk River drainage basin area
is 2249 square miles.
The TVA monitoring station is located at the USGS stream gage near Prospect, Tennessee.
At this location, 1784 square miles or 79 percent of the entire Elk River basin is monitored. Major
tributaries of the Elk River basin include Sugar Creek (177 square miles), Richland Creek (488 square
miles), Cane Creek (106 square miles), Mulberry Creek (99 square miles), and Beans Creek (92
square miles). Tims Ford Dam and Elk River Dam control most of the runoff from the upper quarter
of the watershed.
The Elk River drains an area underlain for the most part by limestone. Consequently, the
water is high in dissolved minerals and fairly hard. About 60 percent of the Elk River basin is
farmland. Urban areas include Pulaski, Fayetteville, Tullahoma, and Winchester, Tennessee.
Ecological Health
The monitoring site on the Elk River, far upstream of any influence of backwater from
Wheeler Reservoir, was rated poor to fair in 1993, a slight improvement over 1992. Improvements
were noted in sediment quality and benthic macroinvertebrates. (Fish were not sampled in 1993.)
Nutrient concentrations were quite high, resulting from phosphorus-rich soils in the watershed. These
high nutrient inflows from the Elk River can stimulate algal blooms in Wheeler Reservoir.
Use Suitability
Bacteriological water quality at an access location about one and one-half miles
downstream of Tims Ford Dam was poor immediately after rainfall, but met recreation criterion if
samples collected within 24-hours of rainstorms were excluded.
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All analytes in fish tissue samples collected in summer 1992 were either not detected or
found in low concentrations.
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9.2 Tims Ford Reservoir
Physical Description
Tims Ford Reservoir in middle Tennessee is formed by Tims Ford Dam at Elk River mile
(ERM) 133.3. The reservoir is 34 miles long at full pool and has a surface area of 10,600 acres.
The depth at the dam is 143 feet and the average depth is about 50 feet. Average annual discharges
from Tims Ford Dam are about 940 cfs, resulting in a hydraulic residence time of about 280 days.
Tims Ford Reservoir is designed for a useful controlled drawdown of 30 feet (895-865 feet MSL) for
flood protection; however, annual drawdowns average about 18 feet.
Ecological Health
The ecological health of Tims Ford Reservoir rated poor-fair (58 percent) in 1993 with
very little change from previous years of Vital Signs monitoring. The most obvious ecological health
problem was the low concentrations of DO near bottom (rated very poor at both the forebay and mid-
reservoir sites in 1993). Although undesirable, low DO concentrations often exist in deep, tributary
storage reservoirs like Tims Ford with long detention times and strong summer stratification. In spite
of these low dissolved oxygen conditions, the fish assemblage rated good at both monitoring sites in
1993. However, the benthos, sampled for the first time in 1993, rated very poor at the forebay and
poor at the mid-reservoir site. Sediment quality, also sampled for the first time in 1993, had high
levels of ammonia at both locations and toxicity to test animals at the mid-reservoir site which rated
poor. Chlorophyll ratings at both locations on Tims Ford Reservoir were good in 1993, indicating
adequate primary productivity to support the food web, but not overly productive, potentially leading
to eutrophic conditions.
Reservoir Use Suitability
Four sites were tested for fecal coliform bacteria in 1992; two sites were retested in 1993
because of high concentrations. The 1993 concentrations were low at the Estill Springs Park, but at
the Dry Fork swimming area, bacteria concentrations were within state criteria only if samples
collected within 24-hours of rainfall are excluded.
There are no fish consumption advisories for Tims Ford Reservoir. All analytes were
either not detected or found in only low concentrations in channel catfish composites collected from
the forebay and transition zone in autumn 1992.
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10.0 r,I INTERS VILLE RESERVOIR - SEQUATCHIE RIVER WATERSHED
This watershed includes Guntersville Reservoir and all tributaries draining directly to
Guntersville Reservoir. As with the other watershed areas on the mainstem of the Tennessee River,
most of the water leaving the watershed through Guntersville Dam enters the watershed area through
discharges from the upstream dam (Nickajack). About 35,900 cfs enter from Nickajack Dam and
about 40,700 cfs is discharged from Guntersville Dam on an annual average basis. The remaining
4800 cfs originates with the Guntersville Reservoir-Sequatchie River watershed area. The largest
contributor of this flow is the Sequatchie River (about 800 cfs). The total watershed area is 2669
square miles. The area drained by the Sequatchie River is about 600 square miles.
Guntersville Reservoir is the dominant characteristic of this watershed. There are three
Vital Signs monitoring site on Guntersville Reservoir: forebay, transition zone, and inflow (Figure
10.1 and Table 2.1). Information from 1993 monitoring activities is provided in Section 10.1.
There is a stream monitoring site on the Sequatchie River at mile 6.3. Monitoring
information for this site for 1993 is provided in Section 10.2.
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Figure 10.1 Map of the Guntersville
Reservoir - Sequatchie River
Watershed Showing Stream and
Reservoir Monitoring sites in
1993.
&
&
Guntersville
Reservoir
'\
\
\
\
\
\
\
A Stream Monitoring Sites
# Reservoir Monitoring Sites
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10.1 Guntersville Reservoir
Guntersville Dam, located at TRM 349.0, creates a 76 mile long reservoir with a surface
area of 67,900 acres and a shoreline of 949 miles at full pool. Average annual discharge is about
40,700 cfs, corresponding to an average hydraulic retention time of about 13 days.
Guntersville Reservoir is similar to Wheeler Reservoir in several size characteristics, but it
differs in one important feature. The average controlled storage volume of Guntersville is about half
that of Wheeler. This is due to the shallow nature of Guntersville Reservoir at the inflow area and
extensive shallow overbank areas. As a result, winter drawdown on Guntersville Reservoir is
nominal to maintain navigation. The shallow drawdown allows the large overbank areas to be
permanently wetted creating good habitat for aquatic macrophytes. Guntersville has the greatest area
coverage of aquatic plants of any TVA reservoir.
The Sequatchie River joins the Tennessee River at about TRM 423, in the upstream
portion of Guntersville Reservoir, just downstream from Nickajack Dam. On the average the
Sequatchie River contributes less than 2 percent to the total flow of the Tennessee River through
Guntersville Reservoir.
Data collected in 1990 and 1991, indicated a more riverine than transition environment at
TRM 396.8. Consequently, in 1992 the transition zone sampling location was relocated further
downstream to TRM 375.2. Results from the new site are being reviewed to determine if it is
suitably located.
Ecological Health
Ecological health conditions were good (78 percent) in Guntersville Reservoir in 1993,
similar to those observed in 1992 (83 percent). All ecological health indicators rated fair, good, or
excellent at all reservoir sites, except for DO at the inflow, which rated very poor (compared to fair
in previous years). A very low DO concentration (1.8 mg/L, the lowest ever recorded in the
discharge from Nickajack Dam) was measured in July and was related to the usual flow patterns
associated with the summer drought and special hydroelectric operations.
As in 1992, 1993 results indicated the transition zone had the best ecological health of the
three sample sites on Guntersville Reservoir. Four of the five aquatic health indicators from this site
had excellent ratings both years; only the fish assemblage rated less than excellent (fair).
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Aquatic macrophytes covered about 7600 acres in 1993 compared to 5993 acres in 1992
and 5165 acres in 1991. Guntersville Reservoir contains more acres of aquatic plants than any other
reservoir in the TVA system.
Reservoir Use Suitability
All sites tested for fecal coliform bacteria in 1992 and 1993 in Guntersville Reservoir met
the Alabama water quality criterion for recreation. At most sites, bacteria concentrations were quite
low. High fecal coliform concentrations were found in the Vital Signs sampling at the forebay in
1990 and 1991, but bacteria concentrations at both the forebay and transition zone were very low in
1992 and 1993.
There are no fish consumption advisories on Guntersville Reservoir. Channel catfish
composites collected from Guntersville Reservoir in autumn 1990 had sufficiently high PCB
concentrations to warrant further examination but were not high enough for the state to issue an
advisory. Catfish collected from the same locations in 1991 and 1992 had progressively lower
concentrations than those from 1990 with the 1992 concentrations generally indicative of
"background" levels found in channel catfish throughout the Tennessee River. Other analytes were
low or nondetectable in the 1992 samples.
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10.2 Sequatchie River Stream Monitoring Site
Physical Description
The Sequatchie River basin is a narrow limestone valley of the Valley and Ridge
physiographic province, surrounded by the Cumberland Plateau to the west and Walden Ridge to the
east. The Sequatchie flows from its headwaters south of the Emory-Obed River basin for more than
110 miles to form an embayment at the upstream end of Guntersville Reservoir, just downstream
from Nickajack Dam. The Sequatchie River drainage basin is 605 square miles.
The TVA monitoring station is located at the Valley Road bridge near Jasper, Tennessee.
The upstream drainage basin is 575 square miles or 95 percent of the entire Sequatchie River basin.
Principal tributaries in the monitored area include the Little Sequatchie River (132 square miles) and
Big Brush Creek (69 square miles).
Dolomite and limestone underlie the floor of the Sequatchie River valley, which is
predominantly farmland. Sandstones underlie the surrounding steep escarpments and plateaus, which
are predominantly forested. Coal mines operate in some areas of the Cumberland Plateau. Whitwell,
Dunlap, and Pikeville, Tennessee, are the primary urban area in the basin.
Ecological Health
The ecological health of the Sequatchie River monitoring site was good in 1993. All
ecological health indicators were either good or fair. Coal mining activities may be hindering the fish
community and bottom-dwelling animals as indicated by deposits of coal fines and other sediments.
Use Suitability
Four canoe sites were sampled in 1992 and 1993 for fecal coliform bacteria. Although
some samples collected after rainfall had high concentrations, all sites met Tennessee water quality
criterion for recreation both years.
Fish tissue samples from the Sequatchie River collected during summer 1992 had
nondetectable or only low concentrations of all analytes.
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11.0 NICKAJACK RESERVOIR - CHICKAMAUGA RESERVOIR WATERSHED
Nickajack and Chickamauga Reservoirs are primary features of this watershed. The
Hiwassee River is the only sizeable tributary which merges with the Tennessee River within the
watershed area. The drainage basin of the Hiwassee River is large enough to be designated a separate
watershed (see Section 12). The remaining area drained by tributaries to these two reservoirs is 1780
square miles. On an annual average basis, about 3200 cfs is contributed to the Tennessee River from
streams within this watershed. This compares to 27,100 cfs entering the upper end of Chickamauga
Reservoir from Watts Bar Dam and 5600 cfs from the Hiwassee River, for a total average annual
discharge from Nickajack Dam of 35,900 cfs.
There are two Vital Signs monitoring sites on Nickajack Reservoir, one at the forebay and
one at the inflow. There is no transition zone site on Nickajack because the reservoir is short and
water exchange is quite rapid. This causes conditions at the location that might be considered the
transition zone to be similar to those at the forebay. Chickamauga Reservoir has four Vital Signs
monitoring sites-the forebay, the transition zone, the inflow, and a new site established in 1993 in the
Hiwassee River embayment (Figure 11.1).
Results from 1993 monitoring activities are in Section 11.1 for Nickajack Reservoir and
11.2 for Chickamauga Reservoir.
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Figure 11.1 Map of the
Nickajack Reservoir -
Chickamauga Reservoir
Watershed Showing
Reservoir Monitoring
Sites in 1993.
Chickamauga
Reservoir
^Hiwassee
River
TN
Nickajack
Reservoir
AL
\
\
\
GA
I Reservoir Monitoring Sites
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11.1 Nickaiack Reservoir
Physical Description
Nickajack Reservoir is one of the smallest reservoirs on the mainstem of the Tennessee
River. With the dam at TRM 424.7, Nickajack has a length of 46 miles, surface area of 10,370
acres, and a shoreline of 192 miles at full pool. Average annual discharge from Nickajack is
approximately 35,900 cfs which provides an average hydraulic retention time of only about three or
four days, the shortest retention time among the reservoirs monitored in this program.
Results from the 1990 and 1991 monitoring indicated that both the forebay and transition
zone sampling sites had quite similar water quality. This was expected since the two sites are
relatively close together (separated by only 7.5 river miles), and Nickajack is a well-mixed, run-of-
the-river reservoir. Therefore, sampling at the transition zone in Nickajack Reservoir was
discontinued in 1992.
Ecological Health
Nickajack Reservoir had a good ecological health rating (88 percent) in 1993, the same as
in 1992 and 1991 (83 percent both years). Nickajack had the highest overall ecological health rating
of all Vital Signs reservoirs in 1993. The only poor rating was for DO at the upper end of Nickajack
Reservoir. This was due to low DOs (minimum 2.2 mg/L) in the releases from Chickamauga Dam in
July 1993. Low DO concentrations had been observed there in previous years, but concentrations
measured in 1993 were the lowest ever recorded from Chickamauga Dam. These concentrations were
not low enough to cause mortality for common species present, but were low enough to affect
organism health and growth. Although the DO rating at the Nickajack forebay was excellent (no DO
concentrations less than 2.0 mg/L were measured), it cannot be concluded that no DO problems
existed. Because low DO concentrations were found in water entering Nickajack Reservoir from
Chickamauga Dam and low DO concentrations were found in water leaving Nickajack Dam, it is
clear that low DOs existed in the Nickajack forebay at some time. The lack of low jneasurements at
the forebay likely is due to the timing of monthly measurements; sampling dates in July and August
bracketed the period with most severe DO problems.
Other than the poor DO rating for the inflow, all other ecological health indicators at the
forebay and inflow sample sites scored good or excellent. Even if low DO concentrations had been
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measured at the forebay, the high scores for the other indicators would have kept the overall rating
for Nickajack Reservoir in the good range.
Aquatic macrophytes on Nickajack Reservoir covered about 1000 acres in 1993 compared
to 830 acres in 1991 to 580 acres in 1992.
Reservoir Use Suitability
The Tennessee Department of Environment and Conservation has issued an advisory that
catfish should not be eaten by children, pregnant women, and nursing mothers because of PCB levels
(about 1.0 uglg); other individuals should limit consumption to no more than 1.2 pounds per month.
Fillets from catfish collected autumn 1992 had PCB concentrations about half those previously found
in the five years of fish tissue studies on Nickajack Reservoir. The study was repeated in autumn
1993 to determine if lower PCB concentrations are found again. Results were not available at the
time this report was prepared.
Fecal coliform bacteria concentrations in areas of Nickajack Reservoir tested during the
recreation site sampling in 1992 and 1993 and Vital Signs sampling since 1990 were generally low.
Exceptions include the boat ramp at Smith's Camp-On-The-Lake, where large populations of geese
probably account for the high concentrations, and North Chickamauga Creek after rainfall.
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11.2 Chickamauga Reservoir
Physical Description
Chickamauga Dam is located at TRM 471.0. The reservoir is 59 miles long, has 810
miles of shoreline, and has a surface area of 35,400 acres at full pool. The average annual discharge
is approximately 34,200 cfs which provides an average hydraulic retention of nine to ten days (Table
4.1).
The Hiwassee River, a major tributary to the Tennessee River, flows into the middle
portion of Chickamauga Reservoir at about TRM 499. The flow from the entire Hiwassee River
watershed contributes approximately 16.5 percent of the flow through Chickamauga Reservoir.
About 10 percent of the 16.5 percent is from the Ocoee River and tributaries in the lower end of the
Hiwassee watershed (i.e., downstream of Apalachia Dam).
Vital Signs monitoring activities were expanded in 1993 to include a site in the Hiwassee
River embayment, which covers about 6500 acres. Given the relatively high flows in the Hiwassee
River (about 5600 cfs annual average), there is substantial water exchange in this embayment, much
greater than in any of the other three embayments monitored.
Ecological Health
The overall ecological health rating for Chickamauga Reservoir was good in 1993 (83
percent), the second-highest rating of all reservoirs. This is an improvement over the fair to good
rating in 1992 (73 percent) and is more like the good rating in 1991 (90 percent). Unlike the other
three reservoirs which had a major embayment monitored for the first time in 1993 (Kentucky,
Pickwick, and Wheeler), results from the Hiwassee River embayment did not lower the overall rating
of Chickamauga Reservoir. Of the five ecological health indicators, two were excellent (chlorophyll
and DO) and three were good (sediment quality, benthos, and fish assemblage) at the Hiwassee
embayment site. If results from the Hiwassee River embayment site were excluded from determining
the overall score for Chickamauga Reservoir, the score would be changed slightly to 81 percent.
Several health indicators had higher ratings in 1993 than in 1992. In particular, the
sediment quality rating improved from poor in 1992 to fair in 1993 at both the forebay and transition
zone. The poor ratings at these two sites in 1992 resulted from elevated concentrations of copper and
zinc and toxicity to test organisms. In 1993 copper and zinc (in addition to trace levels of chlordane)
were again found at the forebay, but no toxicity was found, resulting in a fair rating. The fair rating
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at the transition zone in 1993 was caused by an indication of toxicity (some mortality of rotifers,
although not significantly different from controls) and presence of chlordane in the sediment; copper
and zinc were not elevated. Chlordane in sediments was detected for the first time in 1993. This is
related to improved laboratory methods rather than a true environmental change. New equipment
which allowed better extraction of organic contaminants from sediments was used on 1993 samples.
DO levels on Chickamauga Reservoir were not impacted as much by the hot, dry summer
as on several other Tennessee River reservoirs in 1993. The DO ratings at the forebay and transition
zone were good, but there were small areas during June and July with very low DO concentrations.
These areas are thought to have been too short in duration and too small in area to have had a
significant impact. DO at the inflow rated fair due to a relatively low concentration (3.7 mg/L) in
one sample from the releases of Watts Bar Dam.
Improvements in ratings for both the benthos (poor in 1992 and fair in 1993) and fish
assemblage (fair in 1992 and excellent in 1993) were noted at the inflow. About twice as many
benthic macroinvertebrate taxa were found in 1993 as in 1992, indicating improved conditions. Most
fish assemblage metrics were excellent; this was a distinct improvement over 1992 results. Aquatic
macrophytes on Chickamauga Reservoir covered 1185 acres in 1993 compared to 387 acres in 1992
and 680 acres in 1991. Aquatic macrophytes peaked at about 7500 acres in 1988 and continuously
declined until summer 1993.
Reservoir Use Suitability
There are no fish consumption advisories for Chickamauga Reservoir. Fillets from
Chickamauga Reservoir catfish have been examined for several years as part of a variety of studies.
Study results have indicated no consistent or reservoir-wide problems. Results from most of these
studies have usually found higher concentrations of PCBs in catfish from the inflow area than from
other sites in the reservoir. Channel catfish were collected for screening purposes in autumn 1992
from the inflow, transition zone, and forebay. Concentrations of all analytes from all locations were
low, including PCBs.
No bacteriological studies were conducted at recreation sites on Chickamauga Reservoir in
1993. Bacteriological water quality met the Tennessee criterion for recreation at the ten sites tested in
1989 and 1990. Fecal coliform bacteria concentrations have generally been low at the Vital Signs
locations during all years monitoring activities have occurred.
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12.0 HIWASSEE RIVER WATERSHED
The headwaters of the Hiwassee River extend into the Blue Ridge Mountains in Tennessee,
North Carolina, and Georgia. Streams in this watershed have naturally low concentrations of
nutrients and dissolved minerals. These streams change from steep gradient, cold water trout streams
in the mountains to lower gradient warm water streams in the valley.
The Hiwassee River Watershed has an area of 2700 square miles and an average annual
discharge to the Tennessee River of 5640 cfs. The confluence of the Hiwassee River with the
Tennessee River is in Chickamauga Reservoir at Tennessee River Mile 499.4. The lower portion of
the Hiwassee River is impounded by backwater from Chickamauga Dam. The impounded portion of
the Hiwassee River forms a large embayment (about 6500 surface acres) which extends over 20 miles
up the Hiwassee River.
The largest tributary to the Hiwassee River is the Ocoee River, with a drainage area of
about 640 square miles. Due to past copper mining and industrial activities in the Copperhill area,
several streams and reservoirs in the Ocoee River basin have degraded water quality.
There are eight TVA reservoirs in the Hiwassee River watershed (Figure 12.1 and Table
2.1). Vital Signs monitoring activities are conducted on the five largest reservoirs: Hiwassee
Reservoir (forebay, mid-reservoir, and inflow); Chatuge Reservoir (forebay sites on the Hiwassee
River and Shooting Creek arms); Nottely Reservoir (forebay and mid-reservoir); Ocoee Reservoir No.
1 (forebay only); and Blue Ridge Reservoir (forebay only). Apalachia, Ocoee No. 2, and Ocoee
No. 3 Reservoirs are not included in this monitoring because of their small size.
There is a stream monitoring site on the Hiwassee River at HiRM 36.9, about 2.5 miles
upstream of the confluence of the Ocoee River. A new site will be added in 1994 on the Ocoee River
at mile 2.5. Vital Signs monitoring also includes a site on the Hiwassee River embayment (at
HiRM 10) of Chickamauga Reservoir. Results from that monitoring site are provided in Chapter 11.
Results from 1993 reservoir and stream Vital Signs and Use Suitability monitoring
activities are provided in the following sections:
12.1 Hiwassee Reservoir
12.2 Chatuge Reservoir
12.3 Nottely Reservoir
12.4 Blue Ridge Reservoir
12.5 Ocoee Reservoir No. 1 (Parksville Reservoir)
12.6 Hiwassee River Stream Monitoring Site
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TN
to
<»
I
A Stream Monitoring Sites
9 Reservoir Monitoring Sites
Figure 12.1 Map of the Hiwassee River
Watershed Showing Stream and
Reservoir Monitoring Sites in 1993.
GA
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12.1 Hiwassee Reservoir
Physical Description
Hiwassee Reservoir, in the southwestern corner of North Carolina, is the second-largest of
the five reservoirs in the Hiwassee River watershed included in the Vital Signs monitoring program.
Hiwassee Reservoir is impounded by Hiwassee Dam at river mile 75.8. At full pool level, its
backwater storage pool is about 22 miles long, 6100 acres in surface area, and has a mean depth of
about 69 feet (with a maximum depth of about 255 feet at the dam). It has an average annual
discharge of about 2020 eft and average residence time of about 105 days. Hiwassee Reservoir has
an average annual drawdown of 45 feet.
Ecological Health
Ecological health of Hiwassee Reservoir rated poor-fair (58 percent) in 1993; lower than in
1992 and 1991. The primary factor contributing to reduced ecological health rating was addition of
sediment quality and benthic macroinvertebrates sampling in 1993. Both these indicators rated poor
or very poor at both the forebay and mid-reservoir sites. There were no other poor ratings for any
indicator, not even for DO, which was poor at the forebay in 1992. If scores for these two new
indicators (sediment quality and benthos) were deleted from calculating the overall ecological health
rating for Hiwassee Reservoir, the rating would change substantially to fair-good (72 percent),
consistent with rating for previous years. Poor ratings for sediment quality were due to toxicity to
test organisms and detectable concentrations of chlordane. Most benthos metrics were very poor and
received the lowest score possible.
Like most deep, tributary storage reservoirs with long retention times, thermal
stratification occurs during the summer in Hiwassee Reservoir. During periods of extended thermal
stratification, low concentrations of dissolved oxygen develop near the bottom of the reservoir when
oxygen is consumed by respiration and biochemical processes in the reservoir and in the sediment at a
faster rate than it is replenished by photosynthesis and reaeration from the atmosphere. Although this
low DO area develops in Hiwassee Reservoir, especially in the forebay, it is relatively small. Hence,
DO rated fair at the forebay and good at the mid-reservoir site in 1993.
The upper Hiwassee River watershed is largely forested with few sources of waste to the
river. Consequently, concentrations of nutrients are generally low and primary productivity in the
Hiwassee watershed reservoirs is also generally low. This can be seen in the fair chlorophyll rating
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at the Hiwassee Reservoir forebay in 1993 caused by low chlorophyll concentrations. Chlorophyll
concentrations were just high enough at the mid-reservoir site to rate in the good range. As is
frequently the case in oligotrophic reservoirs, lower standing stocks of fish reflect the small food
base. The fish assemblage rated fair at all locations.
Reservoir Use Suitability
No bacteriological studies were conducted in 1993. In 1990, bacteriological water quality
at four boat ramps was sampled. Fecal coliform bacteria concentrations were very low at all four
sites.
There are no fish consumption advisories on Hiwassee Reservoir. The most recent fish
tissue information is for a channel catfish composite from the forebay collected in autumn 1991. No
pesticide or PCB analytes were detected. With the exception of mercury, metal concentrations in fish
tissue were low or at expected concentrations. The mercury concentration, however, was relatively
high (0.69 fig/g) and so was further investigated in autumn 1993. Both channel catfish and
largemouth bass composites were collected from the forebay and transition zone during autumn 1993.
Results were not available at the time this report was prepared.
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12.2 Chatuge Reservoir
Physical Description
Chatuge Reservoir is located on the Georgia-North Carolina state line in northeastern
Georgia and is formed by Chatuge Dam at Hiwassee River mile (HiRM) 121.0. At full pool
elevation, the reservoir is 13 miles long and has a surface area of about 7000 acres. Its maximum
depth at the dam is 124 feet, and it has a mean depth of 33 feet. An average annual discharge of 459
cfs results in an average hydraulic residence time of about 260 days. Chatuge Reservoir has a
potential useful controlled storage of 23 feet (1928-1905 feet MSL), however, the annual drawdown
averages only ten feet.
Only the forebay of Chatuge Reservoir was monitored prior to 1993. A new monitoring
site was added in 1993 in the Shooting Creek arm to further evaluate this rather large part of the lake.
Because of its physical features, the Shooting Creek site would be expected to be representative of
forebay conditions.
Ecological Health
The ecological health of Chatuge Reservoir rated better in 1993 than in previous years of
Vital Signs monitoring. Chatuge rated fair (67 percent) in 1993 compared to poor-fair in 1992 (56
percent) and 1991 (60 percent). One of the reasons for the higher rating in 1993 was improved
scores for DO, which rated good at the forebay site on the Hiwassee River and fair at the forebay site
on Shooting Creek. In 1992 DO rated poor at the forebay and a mid-reservoir site. Besides an actual
slight improvement in DO conditions, the higher DO rating in 1993 was due to an improvement in the
method for scoring for DO. Also, inclusion of scores for benthic macroinvertebrates, sampled for the
first time in 1993 and rated good at both sample sites, helped to elevate the overall ecological health
rating for Chatuge.
All other indicators (chlorophyll, sediment quality, and fish assemblage) rated fair at both
sample sites. The fair ratings for chlorophyll were due to naturally low concentrations, indicative of
the low availability of nutrients characteristic of the Hiwassee watershed. The fair ratings for
sediment quality were due to toxicity to test organisms at the forebay site on the Hiwassee River and
elevated concentrations of chromium, copper, and nickel at the Shooting Creek site.
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Reservoir Use Suitability
There are no fish consumption advisories on Chatuge Reservoir. The most recent
information available is from a channel catfish composite collected from the forebay in autumn 1991.
None of the pesticide or PCB analytes were detected. Although several metals were detected, they
occurred at low or expected concentrations.
No bacteriological studies were conducted in 1993. In 1990, bacteriological water quality
at three swimming beaches, three boat ramps, and five locations in the middle of the channel were
sampled. Fecal colifonn bacteria concentrations were very low at all sites.
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12.3 Nottelv Reservoir
Physical Description
Nottely Reservoir is formed by Nottely Dam at Nottely River mile 21.0 in northern
Georgia. At full pool elevation, the reservoir is 20 miles long, covers 4200 acres, and has a mean
depth of 40 feet, with a maximum depth of about 165 feet at the dam. Long-term flows from Nottely
Dam average about 415 cfs which result in an average hydraulic retention time of about 206 days.
The annual drawdown averages about 24 feet on Nottely Reservoir.
Ecological Health
The ecological health of Nottely Reservoir rated fair again in 1993 (64 percent), slightly
higher than the fair rating in 1992 and 1991 (60 percent). The primary concern in Nottely Reservoir
is low DO conditions near bottom as evidenced by very poor DO ratings at both the forebay and mid-
reservoir locations in 1993. The only other poor rating for an indicator in 1993 was benthos at the
forebay. Interestingly, the benthos rated good at the mid-reservoir despite the very poor DO
conditions. Chlorophyll rated good at both sample sites in 1993 and sediment quality rated excellent
at the mid-reservoir site. The fish assemblage rated fair at both sample sites in 1993.
Nottely Reservoir's ecological health may not be as good as these monitoring results
suggest, however. For example, there was a fish kill near the dam in the fall of 1992 which was
probably related to low dissolved oxygen. Also, the water in Nottely Reservoir is frequently turbid
due to excessive erosion on the lands surrounding the reservoir. Of the five reservoirs in the
Hiwassee watershed (Hiwassee, Chatuge, Nottely, Blue Ridge, and Ocoee No. 1), Nottely has had the
lowest water clarity, highest chlorophyll concentrations, and highest phosphorus concentrations over
the last three years.
Reservoir Use Suitability
No fish consumption advisories have been issued for Nottely Reservoir. The most recent
fish tissue results are for a channel catfish composite collected from the forebay in autumn 1991. The
only organic analyte detected was PCBs (at a concentration of 0.2 figlg) just above the detection limit.
A few metals were detected but only mercury (0.47 fig/g) was sufficiently high to be of interest.
Similar concentrations have been found, although not consistently, in previous screening studies on
reservoirs in the Hiwassee basin. Both channel catfish and largemouth bass composites were collected
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from the forebay in autumn 1993 and analyzed for mercury to further examine this situation. Results
were not available at the time this report was prepared.
No information was collected for bacteriological contamination at recreation areas on
Nottely Reservoir in 1993. However, the recreation area at Poteet Creek was sampled in 1990 for
fecal coliform bacteria and found to fully support water contact recreation.
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12.4 Blue Ridge Reservoir
Physical Description
Blue Ridge Dam impounds the Toccoa River at mile 53.0 in rural northwest Georgia. The
watershed is mountainous and forested, with a significant portion of the basin lying within the
Chattahoochee National Forest. At full pool, Blue Ridge Reservoir is about 11 miles long, 3300
acres in surface area, and 155 feet deep at the dam, with a average depth of 59 feet. The rate of
discharge of water from Blue Ridge Reservoir averages about 610 cfs, which results in an average
theoretical residence time of about 159 days. The annual drawdown of Blue Ridge Reservoir
averages 36 feet.
Ecological Health
The ecological health of Blue Ridge Reservoir was good in 1993 (72 percent), similar to
that found in 1992 and 1991. Blue Ridge is an oligotrophic reservoir as evidenced by very low
summer chlorophyll concentrations at the forebay, rated fair in 1993. The excellent rating for DO
was in part related to the low primary productivity because a low oxygen demand would be required
to decompose relatively few dead algal cells. The benthic macroinvertebrate community, sampled for
the first time in 1993, rated excellent at the forebay. The fish assemblage rated poor due to low
abundance and diversity, as might be expected in an oligotrophic reservoir. Compared to the other
reservoirs in the Hiwassee watershed, Blue Ridge has had the highest water clarity and lowest
nitrogen concentrations over the three years of Vital Signs monitoring.
Reservoir Use Suitability
There are no fish consumption advisories on Blue Ridge Reservoir. The most recent fish
tissue information from Blue Ridge Reservoir is from a channel catfish composite from the forebay
collected in autumn 1991. Most pesticide and PCB analytes were not detected; those that were,
occurred in low concentrations. Likewise, all metal analytes were either not detected or were found
in low or expected concentrations.
No bacteriological studies were conducted in 1993. In 1990, bacteriological water quality
at one swimming beach was sampled. Fecal coliform bacteria concentrations were very low.
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12.5 Ocoee Reservoir No. 1 fParksville Reservoir")
Physical Description
Ocoee No. 1 Reservoir, also known as Parksville Reservoir, is formed by Ocoee No. 1
Dam at Ocoee River mile 11.9. At full pool elevation, the reservoir has a surface area of about 1900
acres and length of 7.5 miles. Ocoee No. 1 Reservoir is located downstream from the Copper Basin,
and decades of erosion have caused significant filling of the reservoir. Ocoee No. 1 Reservoir has
lost about 25 percent of its original volume, has an average depth of 45 feet and is about 115 feet
deep at the dam. An average annual discharge of about 1400 cfs from Ocoee No. 1 Dam results in a
reservoir retention time of approximately 30 days. Although Ocoee No. 1 Reservoir is not operated
for flood control (only for peaking power generation), its annual drawdown averages about seven
feet.
Ecological Health
The ecological health of Ocoee No. 1 Reservoir rated poor in 1993 (52 percent), with little
change from the previous years of Vital Signs monitoring activities. Four indicators rated poor-
chlorophyll, sediment quality, benthic macro invertebrates, and the fish assemblage. The reservoir is
recovering from years of pollution problems related to copper mining and industrial activities at
Copperhill. Sediment quality, sampled for the first time in 1993, reflected these historic problems
with very high concentrations of copper, lead, and zinc. Also, PCBs were detected in forebay
sediments in 1993.
In spite of the apparent availability of nutrients, algal productivity was low. High DO
concentrations (rated excellent in 1993) existed in Parksville Reservoir throughout the year. High DO
concentrations were present even in the hypolimnion at the forebay. As expected under such
conditions, the fish assemblage rated poor in 1993, comparable to previous years.
Reservoir Use Suitability
There are no fish consumption advisories in effect for Parksville Reservoir. However,
screening studies over the past several years have found PCB concentrations near the level used by
the state of Tennessee to issue a "Limit Consumption" advisory. As a result, TVA and the state
designed and conducted a more detailed sampling of fish in autumn 1992. Results of the 1992 effort
confirmed previous results of relatively high PCB concentrations in channel catfish; the average of ten
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fish was 1.5 fig/g at the forebay and 1.0 figlg at an upper reservoir location. Largemouth bass were
also examined and found to have lower concentrations than catfish; averages at the two sites were 0.6
and 0.7 /zg/g, respectively. Bluegill sunfish and rainbow trout composites from these areas had low
PCB concentrations ("<0.3 /ig/g). The state of Tennessee had taken no action on these results at the
time this report was prepared.
No bacteriological studies were conducted in 1993. In 1991, the swimming area at Mac
Point was surveyed. Fecal coliform bacteria concentrations were low.
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12.6 Hiwassee River Stream Monitoring Site
Physical Description
The headwaters of the Hiwassee River are in the Chattahoochee, Nantahala, and Cherokee
Forests of the Blue Ridge physiographic province. It emerges from the mountains to flow through the
Valley and Ridge province to join the Tennessee River as an embayment of Chickamauga Reservoir.
The TVA monitoring station is located at the Patty Bridge near Benton, Tennessee. The
watershed area above the sampling site is 1300 square miles or 48 percent of the Hiwassee River
basin. Principal tributaries in the Hiwassee watershed include the Valley River (117 square miles),
Nottely River (287 square miles), Conasauga Creek (103 square miles), Toccoa-Ocoee River (639
square miles), Chestuee Creek (132 square miles), and Oostanaula Creek (69 square miles).
Oostanaula Creek, Chestuee Creek, and the Ocoee River are located below this station.
Igneous and metamorphic rocks underlie much of the basin yielding water that is very soft
and low in dissolved minerals. The major urban areas of the Hiwassee River basin include Athens,
Etowah, and Cleveland, Tennessee, in the lower basin. The smaller urban communities of the
mountains include Andrews and Murphy in North Carolina, Blue Ridge and McCaysville in Georgia,
and Copperhill in Tennessee. Runoff from land denuded by historical mining and ore processing near
Copperhill affects water quality in the Ocoee River and its three reservoirs downstream to the
confluence with the Hiwassee River.
Ecological Health
The ecological health of the stream monitoring site on the Hiwassee River was good in
1993, as in 1992. All ecological health indicators (nutrients, sediment quality, benthos, and fish
community) rated either good or fair.
Use Suitability
No fecal coliform samples were collected in 1993. In 1989, the canoe sites, Shallow Ford
Bridge on Toccoa River upstream of Blue Ridge Reservoir, and at Mission Dam on the Hiwassee
River between Chatuge and Hiwassee Reservoirs were sampled. In 1991, the two access locations on
the Ocoee River upstream of Parksville Reservoir, and the three access sites on Hiwassee River
upstream of Chickamauga Reservoir were sampled. Bacteriological water quality at each of the sites
met the appropriate state's criterion for recreation.
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All metal and organic analytes in fish tissue samples were either not detected or found in
low concentrations.
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13.0 WATTS BAR RESERVOIR. FORT LOUDOUN RESERVOIR.
AND MELTON HILL RESERVOIR WATERSHED
This watershed area is relatively small (1370 square miles) and includes three reservoirs:
Fort Loudoun and Watts Bar Reservoirs on the Tennessee River and Melton Hill Reservoir on the
Clinch River. All three are run-of-the-river reservoirs with relatively short retention times and annual
pool drawdowns of only a few feet. The inflow of Fort Loudoun Reservoir is actually the origin of
the Tennessee River. The Holston and French Broad Rivers merge at that point to form the
Tennessee River. The Little Tennessee River, another major tributary to the Tennessee River, enters
Fort Loudoun Reservoir near the forebay. Watts Bar Reservoir is immediately downstream of Fort
Loudoun. The Clinch River, another major tributary, merges with the Tennessee River upstream of
the transition zone on Watts Bar Reservoir. Melton Hill Dam bounds the upper end of Watts Bar
Reservoir on the Clinch River and Fort Loudoun Reservoir bounds it on the Tennessee River.
Like the other watershed areas formed around one or more of the reservoirs on the
mainstream of the Tennessee River, very little of the water leaving this watershed area originates
from within. The average annual discharge through Watts Bar Reservoir is about 27,000 cfis. Of
this, about 25 percent (6800 cfs) enters from the French Broad River, 16 percent (4500 cfs) from the
Holston River, 21 percent (5700 cfs) from the Little Tennessee River, and 15 percent (4200 cfs) from
the Melton Hill Dam on the Clinch River. Another five percent (1400 cfs) is contributed by the
Emory River, a tributary to the Clinch River near the confluence with the Tennessee River. The
remaining 18 percent (4800 cfs) originates from streams which drain directly to one of these
reservoirs.
Vital Signs monitoring activities are conducted at the forebays, transition zones, and
inflows of all three of these reservoirs. Watt Bar Reservoir has two inflow sites, one near Fort
Loudoun Dam and one near Melton Hill Dam. There is one stream monitoring site on the Emory
River at Emory River Mile 18.3 (Figure 13.1).
Results for 1993 monitoring activities are provided in the following sections:
13.1 Watts Bar Reservoir
13.2 Fort Loudoun Reservoir
13.3 Melton Hill Reservoir
13.4 Emory River Stream Monitoring Site
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Figure 13.1 Map of the Watts Bar Reservoir,
Fort Loudoun Reservoir, and Melton Hill
Reservoir Watershed Showing Stream and
Reservoir Monitoring Sites in 1993.
A Stream Monitoring Sites
O Reservoir Monitoring Sites
Fort Loudoun
Reservoir
TN
NC
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13.1 Watts Bar Reservoir
Physical Description
Watts Bar Reservoir impounds water from both the Tennessee River and one of the major
tributaries to the Tennessee River, the Clinch River. The three dams which bound Watts Bar
Reservoir are: Watts Bar Dam located at Tennessee River Mile (TRM) 529.9, Fort Loudoun Dam
located at TRM 602.3, and Melton Hill Dam located at Clinch River mile (CRM) 23.1. The total
length of Watts Bar Reservoir, including the Clinch River arm is 96 miles, the shoreline length is 783
miles, and the surface area is 39,000 acres. The average annual discharge from Watts Bar is
approximately 27,000 cfs, providing an average hydraulic retention time of about 19 days.
The confluence of the Clinch and Tennessee Rivers is upstream of the transition zone
sampling location in Watts Bar, so biological sampling was conducted at the forebay, transition zone,
and both the Tennessee River and Clinch River inflows. Water entering Watts Bar from Melton Hill
Reservoir is quite cool due to the hypolimnetic withdrawal from Norris Reservoir (a deep storage
impoundment) upstream from Melton Hill. Water entering Watts Bar Reservoir from Fort Loudoun
Dam is usually warmer and lower in DO during summer months than water entering from Melton
Hill Dam.
The Emory River is a major tributary to the Clinch River arm of Watts Bar Reservoir and
supplies about 5 percent of the average annual flow through Watts Bar Reservoir. The Tennessee and
Little Tennessee Rivers (i.e., discharge from Fort Loudoun Dam) account for about 75 percent of the
flow, and the Clinch River (i.e., discharge from Melton Hill Dam) accounts for about 15 percent
through Watts Bar Reservoir.
Ecological Health
The ecological health of Watts Bar Reservoir was fair in 1993 (68 percent), similar to
1992 (71 percent) and 1991 (69 percent). Chlorophyll rated good at both the forebay and transition
zone locations. Sediment quality testing at the forebay found low survival of test organisms and high
concentrations of ammonia, leading to a poor rating. A fair to good rating for sediments at the
transition zone was due to traces of chlordane; no other chemical analyte was problematic and no
toxicity was found. Because of the release of water with low DOs from Fort Loudoun Dam, DO
concentrations were less than 5 mg/L (minimum 3.9 mg/L) in the Tennessee River inflow to Watts
Bar Reservoir. Benthic macroinvertebrates rated poor in 1993 at this site (as in both 1992 and 1991),
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possibly related to the low DO concentrations. The fish assemblage was also poor at this inflow site
in 1993. The inflow site on the Clinch River, downstream of Melton Hill Dam, had good DOs, but
the benthos were poor and fish assemblage fair. Compared to 1992, this was a slight decrease for the
benthos, but was similar to the previous results. All aquatic health indicators were good or excellent
at the transition zone, generally similar to 1992 observations.
Aquatic plants have declined from about 700 acres in the late 1980s to about ten acres in
1993.
Reservoir Use Suitability
Fourteen swimming areas were tested for fecal coliform concentrations in 1993. Two
other swimming sites were tested in 1990. Bacteriological water quality was within criteria at 14
sites. The other two sites met criteria if rainfall samples are excluded. Fecal coliform concentrations
at Watts Bar swimming beaches are generally higher than at other Tennessee River Reservoirs.
Monthly fecal coliform bacteria samples have been collected at the Vital Signs locations since 1990.
All samples collected from April through September have been very low.
As a result of PCB contamination, the Tennessee Department of Environment and
Conservation (TDEC) has issued advisories on consumption of several fish species from Watts Bar
Reservoir. In the Tennessee River portion a "do not consume" advisory exists for catfish, striped
bass, and striped bass/white bass hybrids. A precautionary advisory (children and pregnant or
lactating women do not eat fish; all others limit fish consumption to 1.2 pounds per month) is in
effect for largemouth bass, white bass, sauger, carp and smallmouth buffalo. In the Clinch River arm
striped bass should not be eaten, and a precautionary advisory is in effect for catfish and sauger.
Also, TDEC has issued a "do not consume" advisory for fish taken from the east fork of
Poplar Creek due to mercury, metals, and organic chemical contamination.
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13.2 Fort Loudoun Reservoir
Physical Description
Fort Loudoun Reservoir is the ninth and uppermost reservoir on the Tennessee River with
the dam located at TRM 602.3. The surface area and shoreline are relatively small (14,600 acres and
360 miles, respectively) considering the length (61 miles), indicating it is mostly a run-of-the-river
reservoir. The average annual discharge from Fort Loudoun Dam is 18,400 cfs which provides an
average hydraulic retention time of about ten days.
Fort Loudoun Reservoir (and the Tennessee River) is formed by the confluence of the
French Broad and Holston Rivers, with both of these rivers having a major reservoir upstream.
Douglas Dam, 32.3 miles up the French Broad River, and Cherokee Dam, 52.3 miles up the Holston
River, form deep storage impoundments, each having long retention times. Both of these deep
storage impoundments become strongly stratified during summer months resulting in the release of
cool, low DO, hypolimnetic water during operation of the hydroelectric units. Some warming and
reaeration of the water occurs downstream from Cherokee and Douglas Dams, but both temperature
and DO levels are sometimes low when the water reaches Fort Loudoun Reservoir.
Fort Loudoun Reservoir also receives surface waters from the Little Tennessee River, via
the Tellico Reservoir canal, which connects the forebays of the two reservoirs. (Since Tellico Dam
has no outlet, under most normal conditions, water flows into Fort Loudoun Reservoir from Tellico
Reservoir.) Water from Tellico Reservoir (Little Tennessee River) is often cooler and higher in DO,
and has a much lower conductivity than water in Fort Loudoun Reservoir (Tennessee River). In
1992, the forebay sampling location on Fort Loudoun Reservoir (originally located at TRM 603.2)
was moved upstream to TRM 605.5. This resulted in a better assessment of the water quality
conditions of the Tennessee River in the forebay portion of Fort Loudoun Reservoir by minimizing
the effects of the Little Tennessee River and Tellico Reservoir on the data gathered in the forebay of
Fort Loudoun Reservoir.
Although Fort Loudoun Reservoir is a mainstream reservoir, its complex set of hydrologic
conditions (cool water inflows from the Holston, French Broad, and Little Tennessee Rivers) often
causes it to exhibit several characteristics that are more typical of a storage impoundment. In fact,
analysis of historical fisheries data for the Tennessee Valley indicates the fish community of Fort
Loudoun Reservoir is more similar to that in Valley storage impoundments than in other mainstream
reservoirs.
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Ecological Health
Vital Signs monitoring information showed the ecological health of Fort Loudoun
Reservoir was between fair and poor in 1993 (58 percent), basically similar to 1992 (53 percent) and
1991 (60 percent). The only ecological health indicator which rated good or excellent on Fort
Loudoun was DO at the forebay and transitions zone (no data were available from the inflow). Such
good ratings for DO were surprising based on observations of lower DOs in 1993 in other mainstream
reservoirs and historical concerns about DO in Fort Loudoun Reservoir.
Several indicators rated poor or very poor. Sediment quality at the forebay rated poor due
to high zinc concentrations, presence of chlordane, and toxicity to Ceriodaphnia. Transition zone
sediments rated fair with similar conditions as the forebay, but no toxicity to test organisms was
found. These findings are consistent with results found in previous years. The fish assemblage rated
poor at all three sample sites (forebay, transition zone, and inflow) mostly due to low species richness
and low capture rate of individuals (similar to previous years). Benthic macroinvertebrates rated very
poor at the inflow site due to low species richness and abundance (comparable to previous years).
Benthos rated fair at the forebay and transition zone. Similar results had been found at the transition
zone in previous years, but benthic invertebrates at the forebay improved in several metrics,
especially species richness and reduced dominance by tolerant organisms.
Aquatic macrophytes only covered 25 acres on Fort Loudoun Reservoir in 1993.
Coverage over the past decade has ranged 25 to 140 acres.
Reservoir Use Suitability
TDEC has issued advisories on consumption of two fish species from Fort Loudoun
Reservoir. Tennessee advises people not to eat catfish taken from Fort Loudoun Reservoir because of
high levels of PCBs. Also, largemouth bass should not be eaten if they weigh over two pounds or are
caught in the Little River embayment due to PCB contamination.
Fort Loudoun Reservoir has had a PCB problem for more than 20 years. Initially, TVA
and state agencies examined a variety of species from throughout the reservoir to document the
geographical and species variation. The study now continues as a trend study in which there is an
annual collection of catfish from one location. PCB concentrations in catfish have varied over the
years with no distinct trend.
Fecal coliform concentrations at one boat ramp tested in 1993 were within criteria for
recreation. In 1989, 1990, and 1992, fecal coliform samples were collected at a total of three
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swimming beaches and 16 other sites. Bacteria concentrations were low at the swimming beaches and
other sites in the downstream portion of the reservoir. Concentrations in the upstream portion of the
reservoir, especially near downtown Knoxville, were much higher, with four sites exceeding
Tennessee criteria. Fecal coliform concentrations at the monthly Vital Signs locations sampled since
1990 have been very low except for the April 1993 samples.
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13.3 Melton Hill Reservoir
Physical Description
Melton Hill Dam is located at mile 23.1 on the Clinch River and is 56.7 miles downstream
of Norris Dam. Impounded water extends upstream from Melton Hill Dam about 44 miles. Melton
Hill Reservoir has about 170 miles of shoreline and 5690 surface acres at full pool. Average flow
through Melton Hill is about 4900 cfs resulting in an average retention time of approximately 12
days. Melton Hill is TVA's only tributary dam with a navigation lock.
The predominant factor influencing the aquatic resources of Melton Hill Reservoir,
especially the inflow and mid-reservoir areas, is the cold water entering from Norris Dam discharges.
During summer, water discharged from Norris is cold and low in oxygen content. Oxygen
concentrations are improved by a re-regulation weir downstream of Norris Dam and by atmospheric
reaeration in the river reach between Norris Dam and upper Melton Hill Reservoir. However, water
is warmed little and is still quite cool when it enters upper Melton Hill Reservoir. Bull Run Steam
Plant, located at about CRM 47, warms the water some, but water temperatures are still too cool to
support warm water biota and too warm to support cold water biota.
Ecological Health
The ecological health of Melton Hill Reservoir was in the upper end of the fair range in
1993 (68 percent, similar to 1992 and 1991). Chlorophyll and DO were excellent at both the forebay
and the transition zone. However, a poor fish assemblage was found at forebay and inflow, generally
similar to previous years. Primary problems in the fish assemblage were low species richness and
abundance in electrofishing samples. Cool water flowing in from the bottom layer of Norris Lake
causes problems for fish in Melton Hill, especially in the middle and upper sections. The water is too
cold to support fish that like warm water, but too warm to support fish that thrive in cold water. The
benthic macroinvertebrate community rated poor at the forebay and very poor at the transition zone
and inflow, generally similar to previous years. Components of the benthos resulting in poor metrics
were absence of long-lived and intolerant species and dominance by tolerant species.
Aquatic macrophyte coverage on Melton Hill Lake in 1993 was about 240 acres. During
the past decade, coverage has ranged from about 100 to 250 acres.
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Reservoir Use Suitability
No bacteriological studies were conducted at recreation areas in 1993. In 1989, samples
were collected at four boat ramps during a period of high rainfall, and fecal coliform concentrations
were high. In 1990, two swimming beaches and six other sites were tested during a more normal
rainfall period. Concentrations were lower and within recreation criteria. Fecal coliform
concentrations at the monthly Vital Signs locations sampled since 1991 have generally been low.
TDEC has advised the public to avoid consumption of catfish from Melton Hill Reservoir
because of PCB contamination. Samples are collected annually from the transition zone and near the
inflow by TVA and from the forebay by the Oak Ridge National Laboratory as part of ongoing,
cooperative studies. PCB concentrations in catfish collected in autumn 1992 generally fell within the
range found in previous years.
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13.4 Emory River Stream Monitoring Site
Physical Description
The majority of the Emory River drainage area lies in the Cumberland Plateau and flows
through the Tennessee counties of Cumberland, Morgan, and Roane. The Emory River leaves the
plateau and cuts more than 600 feet down the eastern escarpment to join the Clinch River in the
Valley and Ridge physiographic province as a major embayment to Watts Bar Reservoir.
The TVA monitoring station is located at the USGS stream gage at Oakdale. The Emory
River drainage above Oakdale is 764 square miles or 88 percent of the entire Emory River basin.
The principal tributary to the Emory is the Obed River (520 square miles). The principal tributaries
to the Obed are Clear Creek (173 square miles) and Daddy's Creek (175 square miles).
Sandstone, shale, and conglomerates underlie most of the Emory River basin. Most of the
basin is forested. About one-fourth of the basin lies within the Catoosa Wildlife Management Area,
while about 5 percent is used for agriculture and 1 percent is used for surface coal mining. The only
urban area above Oakdale is Crossville, Tennessee, near the headwaters of the Obed River.
Ecological Health
The overall ecological health of the Emory River at the stream monitoring site was good in
1993. This is an improvement over 1992 when fair conditions were found. The primary problem
found in 1992 was poor sediment quality, evidenced by poor survival of test organisms. This was not
the case for 1993 as no sediment toxicity was found.
Use Suitability
There were no bacteriological studies conducted on the Emory River in 1993.
A five fish composite each of carp, channel catfish, and largemouth were collected during
summer 1992 and analyzed for selected metals, pesticides, and PCBs. Only PCBs in channel catfish
were high enough to be of interest. The concentration was near that used to indicate need of more
intensive investigation. Samples collected in summer 1993 should help evaluation of this situation.
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14.0 CLINCH RIVER AND POWELL RIVER WATERSHED
This long, narrow watershed lies in southwest Virginia and northeast Tennessee. Streams
in the watershed have high concentrations of dissolved minerals and generally low concentrations of
nutrients.
For management purposes, an artificial ending point of the watershed has been established
at Norris Dam, which is near Clinch River mile 80. The remainder of the Clinch River is associated
with the Watts Bar, Fort Loudoun, and Melton Hill Reservoir Watershed area. As defined, this
watershed drains an area of 2912 square miles and has an average annual discharge of about 4200 cfs.
The Clinch and Powell Rivers contribute about 80 percent of this flow.
Norris Reservoir is the only major reservoir in the watershed; essentially all streams
upstream from Norris are free flowing. There are three Vital Signs monitoring sites in Norris
Reservoir (forebay and mid-reservoir sites on the Clinch and Powell arms) and two stream sites, one
each on the Clinch and Powell Rivers (Figure 14.1). Results from 1993 monitoring activities are in
Section 14.1 for Norris Reservoir, Section 14.2 for the Clinch River stream monitoring site, and
Section 14.3 for the Powell River stream monitoring site.
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Figure 14.1 Map of the Clinch River
and Powell River Watershed
Showing Stream and Reservoir
Monitoring Sites in 1993.
KY
/ V.WV/' v
VA
Stream Monitoring Sites
Reservoir Monitoring Sites
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14.1 Norris Reservoir
Physical Description
Norris Reservoir is formed by Norris Dam at Clinch River mile (CRM) 79.8. It is a
large, dendritic, tributary storage impoundment of the Clinch and Powell Rivers which flow together
about nine miles upstream of the dam. Norris is one of the deeper TVA tributary reservoirs, with
depths over 200 feet. Annual drawdown averages about 32 feet. At full pool, the surface area of the
reservoir is 34,200 acres, the shoreline is about 800 miles in length, and water is impounded 73 miles
upstream on the Clinch River and 53 miles upstream on the Powell River. Norris Reservoir has a
long average retention time (about 245 days) and an average annual discharge of approximately 4200
cfs. Due to the great depth and long retention time of Norris Reservoir, significant vertical
stratification is expected. Additional information about the physical and hydrologic characteristics of
Norris Reservoir are given in Table 4.1.
Because of the confluence of the Clinch and Powell Rivers relatively close to the dam,
thTee reservoir sampling locations were established: one forebay site; and two mid-reservoir sites-
one on the Clinch River and one on the Powell River.
Ecological Health
Norris is an oligotrophic reservoir with very clear water. There is little algal primary
production because of phosphorus limitations. The ecological health of Norris Reservoir in 1993 was
fair (67 percent), with conditions about the same as in 1992 and 1991 (60-67 percent). Dissolved
oxygen concentrations in the deeper portions of Norris Reservoir, particularly at the mid-reservoir
locations on the Clinch and Powell Rivers, have historically been low. This condition, although
undesirable, is often observed in deep, thermally stratified tributary reservoirs with long retention
times.
As expected, 1993 DO concentrations rated very poor at both mid-reservoir sites. The
rating for DO at the forebay was poor in 1993 compared to fair in 1992. The 1992 results had
indicated a slight improvement over 1991 conditions.
As in the past, low nutrient concentrations in the forebay resulted in low algal levels and a
fair rating for chlorophyll in 1993. The effects of low primary productivity usually manifests itself
throughout the food chain and results in a low overall abundance of fish. The fish assemblage rated
fair at the forebay in 1993, primarily due to low abundance and low species richness. At both mid-
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reservoir sites, both chlorophyll and fish assemblages rated good. The benthic macroinvertebrate
community rated fair at the forebay and mid-reservoir site on the Clinch arm of Norris Reservoir and
good at the mid-reservoir site on the Powell arm. Given the low DO concentrations near the bottom,
fair to good ratings for benthic macroinvertebrates are better than would be expected. This suggests
that the benthic community is able to recover quickly between autumn reoxygenation of bottom
sediments and sample collection the following spring. Another possible explanation is that some of
the samples collected along the transect were above the oxygen-stressed stratum. Results from
individual samples suggest both factors contributed to the observed ratings.
Reservoir Use Suitability
There are no fish consumption advisories on Norris Reservoir. Channel catfish were
collected for screening purposes in autumn 1992. All analytes were low or not detected except PCBs.
The highest PCB concentration was 0.9 uglg. Concentrations this high had not been found before.
Areas were resampled in autumn 1993 to further examine PCB concentrations, but results were not
available at the time this report was prepared.
Fecal coliform bacteria samples were collected at five sites in 1993. Concentrations were
very low at all five sites. In 1991, ten sites were sampled. Fecal coliform concentrations were
generally higher in 1991 than in 1993, possibly due to higher rainfall in 1991. However, in 1991 all
sites met the geometric mean bacteriological water quality criterion for recreation. In 1991 three sites
exceeded one of EPA's recommended guidelines; more than 10 percent of the samples had fecal
coliform concentrations greater than 400/100 mL. Fecal coliform sampling at the Vital Signs
locations was discontinued in 1993. Fecal coliform concentrations at the three Vital Signs stations
sampled from 1990 to 1991 were very low.
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14.2 Clinch River Stream Monitoring Site
Physical Description
The TVA stream monitoring station is located at the USGS stream gage near Tazewell,
Tennessee, just upstream of the impounded water of Norris Reservoir, at CRM 159.8. The Clinch
River basin above the monitoring site is 1474 square miles or 33 percent of the total Clinch River
basin. Three-quarters of the monitored area lies within Virginia. Principal tributaries in the
monitored area are the North Fork Clinch River (87 square miles), Guest River (102 square miles),
Little River (126 square miles), Copper Creek (133 square miles), and Big Cedar Creek (86 square
miles).
The headwaters of the upper Clinch River drain the eastern escarpment of the Cumberland
Plateau (including portions of the Jefferson National Forest), then flow southwest through the Valley
and Ridge physiographic province in a valley parallel to and southeast of the Powell River. Land use
in the basin is 70 percent forestry and 30 percent agriculture. Coal mining occurs in some areas.
Ecological Health
The overall ecological health of the Clinch River at this site was good as in 1992.
Conditions for fish and bottom-dwelling animals remained good in 1993. Sediment quality showed an
improvement over 1992, with the rating changing from fair to good.
Use Suitability
Concentrations of fecal coliform bacteria were very low in 1993 at the weir and canoe
launch site in the Clinch River downstream of Norris Dam. Concentrations were higher in 1991
when the canoe launch site had been tested.
All analytes in fish tissue samples collected during summer 1992 were either not detected
or found in low concentrations.
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14.3 Powell River Stream Monitoring Site
Physical Description
The Powell River joins the Clinch River 10 miles upstream from Norris Dam and forms a
major embayment to Norris Reservoir. Most of the Powell River headwaters and tributary streams
drain portions of the eastern border of the Cumberland Plateau, but the main river is predominantly in
the Valley and Ridge physiographic province. The river flows for more than 195 miles through
southwestern Virginia and northeastern Tennessee. The total drainage of the Powell River basin is
938 square miles.
The TVA monitoring station is located near Arthur, Tennessee. Above this location the
area of the basin is 685 square miles or 73 percent of the entire Powell River watershed. Principal
tributaries above Arthur include Indian Creek (66 square miles) and the North Fork Powell River
(90 square miles).
Land use in the basin is 75 percent forest, 20 percent agriculture, and almost 5 percent
surface mining, primarily in the upper reaches in southwestern Virginia. Only small urban areas are
located in the Powell River watershed.
Ecological Health
Conditions for fish and bottom-dwelling animals improved to good in 1993. The change
from a fair to a good classification was a result of greater numbers and higher quality bottom-
dwelling organisms present. The Powell River watershed is heavily mined for coal and has a history
of illegal discharges of blackwater into the river from coal washing facilities.
Use Suitability
There were no bacteriological studies conducted on the Powell River in 1993.
All analytes in fish tissue samples collected in summer 1993 wre either nondetectable or
found low concentrations.
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15.0 LITTLE TENNESSEE RIVER WATERSHED
The Little Tennessee River Watershed encompasses 2672 square miles, mostly in
Tennessee and North Carolina with a small area in Georgia. Much of the watershed is forested, with
the headwaters in the Blue Ridge Mountains. The basin is underlain mostly by crystalline and
metasedimentary rocks of the Blue Ridge province. This watershed is home to a large variety of
federally listed threatened and endangered species.
Most of the streams in the watershed are steep gradient and generally have low
concentrations of both dissolved minerals and nutrients. The two largest tributaries to the Little
Tennessee River are the Tuckasegee River which merges with the Little Tennessee in Fontana
Reservoir and the Tellico River which merges with the Little Tennessee in Tellico Reservoir.
There are several reservoirs in the watershed but only Fontana Reservoir in the
mountainous area and Tellico Reservoir at the lower end of the watershed are monitored (Figure
15.1). TVA does not monitor the other reservoirs either because of their small size or because they
are owned by the Aluminum Company of America (ALCOA).
Two sites are monitored on Tellico Reservoir (the forebay and transition zone) and three
sites on Fontana Reservoir (the forebay and mid-reservoir sites on the Little Tennessee River and
Tuckasegee River). There is one stream monitoring site in the watershed, on the Little Tennessee
River upstream of Fontana Reservoir. Another stream monitoring site (on the Tuckasegee River) is
being added in 1994. Results of 1993 monitoring activities are provided in the following sections:
15.1 Tellico Reservoir
15.2 Fontana Reservoir
15.3 Little Tennessee River Stream Monitoring Site
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Figure 15.1 Map of the Little
Tennessee River Watershed
Showing Stream and
cr>
to
~ Stream Monitoring Sites
• Reservoir Monitoring Sites
-------
15.1 Tellico Reservoir
Physical Description
Tellico Dam is located on the Little Tennessee River just upstream of the confluence of the
Little Tennessee and Tennessee Rivers. It is the last dam completed in the TV A system with dam
closure in 1979. Tellico Reservoir is 33 miles long, has a shoreline of 373 miles, and has a surface
area of about 16,000 acres at full pool. The average estimated flow through Tellico Reservoir is
approximately 5700 cfs which provides an average retention time of about 37 days. Very little of this
water is discharged through Tellico Dam. Rather, it is diverted through a navigation canal to Fort
Loudoun Reservoir near the dam for hydroelectric power production. Water characteristics in these
two reservoirs differ considerably as discussed in Section 13.2, Fort Loudoun Reservoir. The
hydrodynamics and exchange of water via the inter-connecting canal significantly affect water quality
within Tellico Reservoir (and Fort Loudoun Reservoir). The canal is only 20-25 feet deep, but the
depth of Tellico Reservoir at the forebay is about 80 feet. Thus, water at strata below about 25 feet
is essentially trapped and becomes anoxic during much of the summer in the forebay of Tellico
Reservoir.
The impounded water of Tellico Reservoir extends upstream of the confluence of the Little
Tennessee and Tellico Rivers. The transition zone site selected for sample collection in 1990, 1991,
and 1992 was in the Little Tennessee River, just upstream of the confluence with the Tellico River at
Little Tennessee River Mile (LTRM) 21.0. Water conditions at that site are largely controlled by
discharges from Chilhowee Dam at LTRM 33.6. This water is cold, nutrient poor, and has a low
mineral content, conditions that are not conducive to establishing a diverse, abundant aquatic
community. In 1993, the transition zone sampling location in Tellico Reservoir was moved six miles
downstream to LTRM 15.0, just below the confluence of the Tellico River-a site more characteristic
of lacustrine rather than riverine conditions.
Ecological Health
Tellico Reservoir received a better ecological health rating in 1993 than in previous years.
The rating was 63 percent (fair) for 1993 compared to 48 percent in 1992 and 44 percent in 1991
(both poor). The primary causes of the higher score were better ratings for DO at the forebay
(mostly the result of an improved, more accurate method of calculating the score for this indicator)
and addition of information from the transition zone collection site which was relocated in 1993. The
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change in DO scoring resulted in forebay DO being rated fair in 1993, whereas it had preciously been
rated poor every year. Other than that change, all indicators at the forebay rated the same in 1993 as
in previous years—poor sediment quality and benthic macroinvertebrate community, good chlorophyll,
and fair fish assemblage.
Two indicators, chlorophyll and DO, received excellent ratings at the new transition zone
site. The other three rated poor-sediment quality (presence of chlordane and significant toxicity),
benthos (mostly due to absence of long-lived and sensitive organisms), and fish assemblage (few fish
collected in gill netting efforts, which affected several metrics).
The higher ecological health score for 1993 is considered to be more representative of the
true environmental conditions in Tellico Reservoir than previous scores.
Most of the 246 acres of aquatic macrophytes on Tellico Lake in 1993 were in the Tellico
River arm of the reservoir.
Reservoir Use Suitability
No bacteriological studies were conducted at recreation areas in 1993. In 1992, fecal
coliform samples were collected at four swimming beaches and five other sites on the reservoir.
Bacteria concentrations were low. Fecal coliform concentrations at the monthly Vital Signs locations
sampled since 1991 have been very low.
The state has advised that catfish from Tellico Reservoir should not be eaten because of
PCB contamination. Fish were collected in autumn 1992 for tissue analysis. Channel catfish were
collected as part of a continuing effort to examine the trend in PCB concentrations. Results indicate
the PCB problem continued to exist with no downward trend.
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15.2 Fontana Reservoir
Physical Description
Fontana Reservoir is located in the Blue Ridge Mountains of western North Carolina.
Fontana is the deepest reservoir in the TVA system. At full pool it has a maximum depth of 460
feet, a length of 29 miles, a shoreline of 248 miles, and a surface area of 10,640 acres. Fontana
Reservoir has a relatively large drawdown, which averages about 64 feet annually. Every fifth year
Fontana is drawn even deeper to allow sluice gate access for maintenance.
Fontana Dam is located at Little Tennessee River Mile 61.0. Average annual discharge is
3840 cfs which provides an average hydraulic retention time in the reservoir of 186 days.
Water in Fontana Reservoir is quite clear due to limited photosynthetic activity and a
mostly forested watershed. Water entering the reservoir is low in nutrients and dissolved minerals.
Ecological Health
Fontana Reservoir rated fair in 1993 (64 percent), the first year of Vital Signs monitoring.
Fontana is an oligotrophic reservoir with very low chlorophyll concentrations resulting in fair ratings
at all three sites. Further evidence of the low primary productivity is the clear, blue water (indicating
low abundance of algae and lack of green phytoplankton pigments). Secchi depths averaged almost
6 meters in the forebay of Fontana in 1993. The fish assemblage also rated fair at all locations,
probably related to the low primary productivity. Ratings for DO varied from excellent at the mid-
reservoir site on the Little Tennessee River to poor at the mid-reservoir site on the Tuckasegee River,
with a fair rating at the forebay. Sediment quality also varied greatly among the three locations—poor
at the forebay, good at the mid-reservoir site on the Tuckasegee arm, and excellent on the Little
Tennessee arm. Rating for the benthic macroinvertebrate community also varied greatly from very
poor at the forebay to fair at the Little Tennessee River mid-reservoir site. The benthos rating at the
forebay was not included in determining the overall ecological health score because part of the
transect sampled was in the drawdown zone.
Reservoir Use Suitability
Channel catfish were collected in autumn 1992 from the forebay and mid-reservoir site on
the Little Tennessee River. Analysis of composited fillets from each area found most analytes were
not detected or had low concentrations. The exceptions to this were mercury at both locations
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(maximum of 0.53 uglg) and PCBs at the forebay (1.1 fig/g). Channel catfish were collected again in
1993 from both locations and analyzed for the same analytes with close attention for PCBs at the
forebay. Largemouth bass were also collected in autumn 1993 from both locations to further examine
mercury concentrations. Results were not available at the time this report was prepared.
There were no bacteriological studies conducted on Fontana Reservoir in 1993.
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15.3 Little Tennessee River Stream Monitoring Site
Physical Description
The Little Tennessee River drains 2727 square miles and flows more than 140 miles
through the Blue Ridge physiographic province of western North Carolina and the Valley and Ridge
province of East Tennessee. It joins the Tennessee River near Lenoir City, Tennessee.
The TV A monitoring station is located near Needmore, North Carolina. The drainage area
upstream from the monitoring site is 440 square miles or 16 percent of the entire Little Tennessee
River basin. Principal tributaries to the Little Tennessee River include Abrams Creek (88 square
miles), Cheoah River (215 square miles), Nantahala River (175 square miles), Cullasaja River (93
square miles), and the Tuckasegee-Oconaluftee River (734 square miles). The Cullasaja River is the
only major tributary within the monitored area. The basin has been extensively developed with TVA
reservoirs (Tellico and Fontana) and private power dams (Chilhowee, Calderwood, Cheoah,
Santeetlah, Nantahala, Franklin, and Thorpe).
Igneous and metamorphic rock underlies all of the basin. Much of the basin is located
within the federally managed lands of the Great Smoky Mountains National Park and Cherokee and
Nantahala National Forests. Franklin, Sylva, Bryson City, and Robbinsville, North Carolina, are the
primary urban areas in the basin.
Ecological Health
The stream monitoring site on the Little Tennessee River (at LTRM 94.5) had a very good
ecological health rating in 1993 (as in 1992). All indicators (nutrients, sediment quality, benthos, and
fish) were rated good.
Use Suitability
No bacteriological studies have been conducted in the streams of this watershed under this
monitoring program.
All analytes in fish tissue samples collected during summer 1993 were either below
detection limits or found in low concentrations.
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16.0 FRENCH BROAD RIVER WATERSHED
The French Broad River watershed is one of the largest (5124 square miles) watersheds in
the Tennessee Valley. About half the watershed is in Tennessee and half is in North Carolina. The
French Broad River and its two large tributaries (Nolichucky and Pigeon Rivers) originate in the Blue
Ridge Mountains. All three of these rivers merge at the upper end of Douglas Reservoir, the only
sizable reservoir in the watershed. The water in the French Broad River is moderately hard and
relatively high in nutrients.
There are three reservoir Vital Signs monitoring sites on Douglas Reservoir and one
stream monitoring site each on the French Broad and Nolichucky Rivers (Figure 16.1). A stream
monitoring site on the Pigeon River is being added in 1994. All stream monitoring sites are upstream
of Douglas Reservoir.
Results from 1993 Vital Signs monitoring activities are provided in the following sections:
16.1 Douglas Reservoir
16.2 French Broad River Stream Monitoring Site
16.3 Nolichucky River Stream Monitoring Site
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Figure 16.1 Map of the French Broad River
Watershed Showing Stream and Reservoir
Monitoring Sites in 1993.
TN
*31
Douglas
Reservoir
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A Stream Monitoring Sites
• Reservoir Monitoring Sites
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16.1 Douglas Reservoir
Physical Description
Douglas Reservoir is a deep storage impoundment (tributary reservoir) on the French
Broad River. Douglas Dam is located 32.3 miles upstream of the confluence of the French Broad and
Holston Rivers which form the Tennessee River. Reservoir drawdown during late summer and
autumn is rather large, with an annual average of about 48 feet. The large annual fluctuation in
surface water elevation causes other physical characteristics such as surface area, reservoir length, and
retention time to vary greatly during the year. At full pool, maximum depth at the dam is 127 feet,
surface area is 30,400 acres, the shoreline is 555 miles, and the length is 43 miles. Average annual
discharge is approximately 6780 cfs, which provides an average hydraulic retention time of about 105
days.
Lengthy retention times and lack of mixing due to their deep nature tend to cause storage
impoundments to have strong thermal stratification during summer months. Undesirable conditions
often develop in the hypolimnion due to anoxia, which in most cases extends from the forebay to the
mid-reservoir sampling location.
Ecological Health
The ecological health of Douglas Reservoir was fair to poor (58 percent) in 1993, with
little change compared to 1991 and 1992. Factors adversely affecting the ecological health of
Douglas Reservoir were strong thermal stratification and high nutrient loadings. This combination
results in hypolimnetic anoxia and release of iron and manganese, phosphorus, and ammonia from the
sediment and excessive eutrophication of the reservoir. Ratings for DO were very poor at both the
forebay and mid-reservoir sites in 1993 due to very low hypolimnetic DO at both locations and low
surface DO at the forebay. This hypolimnetic anoxia promoted the release of ammonia (and sulfide)
from the sediment and negatively impacted the benthic community. The benthic macroinvertebrates
rated poor at the forebay (samples were not collected from the mid-reservoir site). Sediment quality
rated good at the forebay but poor at the mid-reservoir site. The fish assemblage was fair at the
forebay and good at the mid-reservoir site. Chlorophyll rated good at the forebay, but only fair at the
mid-reservoir site because concentrations were relatively high, indicative of high nutrients and high
primary productivity.
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Reservoir Use Suitability
There are no fish consumption advisories on Douglas Reservoir. However, fish from the
Pigeon River upstream of Douglas Reservoir should not be eaten because of dioxin contamination.
The most recent collection of fish from Douglas Reservoir was in autumn 1992. TVA collected fish
samples and provided fillets to the Tennessee Department of Environment and Conservation for
analysis. Results were not available at the time this report was prepared.
Fecal coliform concentrations were very low at the swimming beach and two boat ramps
tested in 1993. Fecal coliform bacteria sampling at the two Vital Signs stations was dropped in 1993.
From 1990 to 1992, concentrations were very low.
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16.2 French Broad River Stream Monitoring Site
Physical Description
The French Broad River is a major tributary to the Tennessee River system, flowing
westward out of the Appalachian Mountains for more than 220 miles to meet the Holston River and
form the Tennessee River.
The drainage basin above the stream monitoring site at the USGS stream gage at near
Newport, Tennessee, is 1858 square miles or 36 percent of the watershed. Principal tributaries in the
monitored area include Big Laurel Creek (132 square miles), Ivy Creek (161 square miles), the
Swannanoa River (133 square miles), Hominy Creek (104 square miles), and Mud Creek (113 square
miles). Two major tributaries enter the French Broad River below the monitoring site. They include
the Nolichucky River (1756 square miles) and the Pigeon River (689 square miles).
Ecological Health
The ecological health of the stream monitoring site at the French Broad River site rated
poor in both 1993 and 1992. Nutrients rated poor because of high concentrations of phosphorus.
Inflows of nutrients promote the excessive algal productivity in Douglas Reservoir. The fish
community on the French Broad River was poor in 1993, same as in 1992. Given the poor water
quality of the Nolichucky and French Broad Rivers flowing into Douglas Reservoir, the poor-fair
ecological health of the reservoir is not unexpected. Together the Nolichucky and French Broad
Rivers provide about 75 percent of the total inflow to Douglas Reservoir.
Use Suitability
No bacteriological studies were conducted as part of the monitoring program in 1993. All
analytes in fish tissue samples collected during summer 1993 were either not detected or found in low
concentrations.
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16.3 Nolichuckv River Stream Monitoring Site
Physical Description
The Nolichucky River is a major tributary to the French Broad River basin and joins the
French Broad River at the upstream end of Douglas Reservoir. The Nolichucky River Basin is 1756
square miles. The upper portion of the basin (approximately 60 percent) lies in the Blue Ridge
physiographic province while the remainder lies in the Valley and Ridge province.
The stream monitoring location is at the TV A stream gage at the David Thomas bridge
near Lowlands, Tennessee. The Nolichucky River basin above the monitoring site is 1686 square
miles or 96 percent of the entire Nolichucky River basin. Principal tributaries in the monitored area
include North Toe River (442 square miles) and Cane River (158 square miles) in the Blue Ridge
physiographic province and Lick Creek (266 square miles) in the lower Valley and Ridge province.
The upper portion of the Nolichucky River basin is primarily forested, while the lower
portion is agricultural. High concentrations of solids from mica and feldspar mining and processing
near Spruce Pine on the North Toe River have severely impacted the streambed downstream. In
addition to Spruce Pine, other urbanized areas include Greeneville and Erwin, Tennessee.
Ecological Health
The overall ecological health of the Nolichucky River at this site was good in 1993, as
opposed to fair in 1992. The change was driven by improvements in the fish community, the absence
of acute sediment toxicity, and improvements in nutrient concentrations. The conditions for bottom-
dwelling animals remained unchanged.
Use Suitability
Bacteriological studies were not conducted as part of this monitoring program in this
watershed in 1993.
All analytes in fish tissue samples collected during summer 1993 were either not detected
or found in low concentrations.
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17.0 HOLSTON RIVER WATERSHED
The Holston River Watershed encompasses 3776 square miles, mostly in upper east
Tennessee and southwest Virginia and a small area in North Carolina. The area is relatively highly
populated with substantial industrial development.
Much of the area is underlain with limestone and dolomite which results in high
concentrations of dissolved minerals in the streams. There is also substantial zinc mining in the
watershed.
There are several reservoirs in the watershed with varying size, depth, flow, and water
quality characteristics. The largest is Cherokee Reservoir on the Holston River near the lower end of
the watershed. The uppermost reservoirs are Watauga Reservoir on the Watauga River and South
Holston Reservoir on the South Fork Holston River. Downstream from these reservoirs, the Watauga
and South Holston Rivers merge in Boone Reservoir. Immediately downstream from Boone Dam is
Fort Patrick Henry Reservoir, the smallest of the five reservoirs in this watershed included in the
Vital Signs Monitoring Program. A few miles downstream from Fort Patrick Henry Dam the South
Fork and North Fork Holston Rivers merge to form the Holston River.
Vital Signs monitoring activities are conducted at one, two, or three locations depending
on reservoir size and characteristics (Figure 17.1). There is also a stream monitoring site on the
Holston River upstream of Cherokee Reservoir.
The average annual discharge from Cherokee Dam is 4460 cfs. The Holston River merges
with the French Broad River at Knoxville to form the Tennessee River.
Results from Vital Signs monitoring activities in 1993 are in the following sections:
17.1 Cherokee Reservoir
17.2 Fort Patrick Henry Reservoir
17.3 Boone Reservoir
17.4 South Holston Reservoir
17.5 Watauga Reservoir
17.6 Holston River Stream Monitoring Site
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Figure 17.1 Map of the Holston River
Watershed Showing Stream and Reservoir
Monitoring Sites in 1993.
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17.1 Cherokee Reservoir
Physical Description
Cherokee Reservoir is formed by Cherokee Dam at Holston River mile (HRM) 52.3. Like
Norris and Douglas Reservoirs, it is a large, relatively deep, tributary storage impoundment with a
substantial drawdown which begins in late summer. When the water surface is at full pool, maximum
depth at the dam is 163 feet and winter drawdown is 53 feet. However, full pool is not reached most
years, and the long-term average drawdown is about 28 feet. At full pool, Cherokee Reservoir is 54
miles long, has a surface area of 30,300 acres, and a shoreline of 393 miles. Average annual
discharge is about 4500 cfs which provides an average hydraulic retention time (at full pool) of
approximately 165 days.
Like other deep storage impoundments with long retention times, Cherokee Reservoir
exhibits strong vertical stratification during summer months. The hypolimnetic oxygen deficit on
Cherokee is one of the worst of all Vital Signs monitoring reservoirs and has been well documented
in numerous past studies (Iwanski, 1978; Iwanski et al., 1980; Hauser et al., 1987).
Ecological Health
The ecological health of Cherokee Reservoir rated fair (64 percent) in 1993, which was
higher than poor ratings in 1992 (55 percent) and poor to fair ratings in 1991 (60 percent). The
improved ecological health rating compared to 1992 resulted mostly from addition of benthic
macroinvertebrate information from the upper reservoir sample site, and from slight improvements
(decreases) in chlorophyll concentrations at the mid-reservoir site. Although benthos data were
collected from Cherokee Reservoir in 1992, ratings were not available for 1992 results because of an
insufficient data base to establish expected (reference) conditions for the benthic macroinvertebrate
community in tributary storage reservoirs. Additional benthos sampling in 1993 on Cherokee plus
several other similar reservoirs provided sufficient data to establish at least preliminary expectations
for reservoirs of this type. The benthic community rated fair at the forebay and excellent at the upper
monitoring site indicating very good conditions there. Improvements noted for chlorophyll at the
mid-reservoir site in 1993, rated good compared to fair in 1992 (due to high averages during
summer), also helped elevate the overall ecological rating in 1993 compared to 1992.
A problem consistently found in Cherokee Reservoir is very low DO concentrations at the
forebay and mid-reservoir sites. Both rated very poor in 1993. This near-bottom low dissolved
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oxygen condition, often observed in deep tributary reservoirs with long retention times, is especially
severe in Cherokee Reservoir, resulting in high concentrations of un-ionized ammonia in sediment.
The fair fish community observed at all monitoring sites in 1993 was probably also influenced to
some extent by the low oxygen concentrations in Cherokee Reservoir. Sediment quality rated poor at
the mid-reservoir site due to high ammonia and copper concentrations coupled with significant toxicity
to rotifers.
Reservoir Use Suitability
There are no fish consumption advisories on Cherokee Reservoir. Channel catfish for
screening tissue analysis were collected in autumn 1992. All analytes were not detected or found in
low concentrations except PCBs. Maximum PCB concentrations were 0.8 /zg/g at the forebay in
1992. Screening samples were collected again in 1993 to further examine PCB concentrations, but
results were not available at the time this report was prepared.
Fecal coliform concentrations were low at all test sites in 1993-a swimming beach, seven
boat ramps, and one other site tested. Fecal coliform bacteria sampling at the two Vital Signs stations
was discontinued in 1993. From 1990 to 1992, concentrations were very low.
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17.2 Fort Patrick Henry Reservoir
Physical Description
Fort Patrick Henry Reservoir is one of the smaller reservoirs included in the Vital Signs
Monitoring Program. It is only ten miles long, has a surface area of about 870 acres, and has a
shoreline of 37 miles. Although it is a tributary reservoir, it has characteristics of a run-of-river
reservoir, rather than a storage reservoir. Annual fluctuation in elevation is only five feet. Also,
retention time is short; with an average discharge of 2650 cfs, the hydraulic retention time is only
about five days. Maximum depth is about 80 feet. Fort Patrick Henry Dam is located at South Fork
Holston River mile 8.2.
This reservoir had not been sampled as part of this monitoring effort prior to 1993.
Because of its small size, only the forebay is monitored for Vital Signs.
Ecological Health
The ecological health of Fort Patrick Henry Reservoir was fair to good (72 percent) in
1993. DO was the only indicator which rated excellent and sediment quality was the only indicator
which rated good. Chlorophyll rated fair, with the average annual concentration only slightly above
the level considered good. The benthos and fish assemblage also rated fair.
Reservoir Use Suitability
Fecal coliform concentrations at Warriors Path State Park were within Tennessee's criteria
for recreation during 1993 studies. TVA's first fish tissue studies on this reservoir were conducted in
autumn 1993; results were not available at the time this report was prepared.
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17.3 Boone Reservoir
Physical Description
Boone Dam is located at South Fork Holston River mile (SFHRM) 18.6, approximately
1.4 miles downstream of the confluence of the South Fork Holston and the Watauga Rivers. At
normal maximum pool (1384 feet MSL), Boone Reservoir extends upstream approximately 17.4 miles
on the South Fork Holston River and 15.3 miles on the Watauga River for a total reservoir length of
approximately 32.7 miles. Boone Reservoir has a surface area of 4300 acres, a shoreline length of
approximately 122 miles, an average depth of 44 feet, and a maximum depth of 129 feet near the
dam. Annual average discharge from Boone Dam is about 2500 cfs, which results in an average
hydraulic residence time of about 38 days. Annual drawdowns of Boone Reservoir usually average
about 25 feet.
Three locations were selected for ecological health monitoring in Boone Reservoir, one at
the forebay and two mid-reservoir sampling locations, one on the Watauga River arm and one on the
South Fork Holston River arm. Sediment and benthic macroinvertebrate sampling were added for the
first time in 1993.
Ecological Health
The ecological health evaluation of Boone Reservoir was lower in 1993 compared to 1992.
The rating for 1993 was toward the low end of the fair range (59 percent) whereas it was in the
middle of the range in 1992 (64 percent). Ecological health ratings in both 1992 and 1993 were
higher than in 1991 when poor conditions were found (51 percent). Primary contributors to lower
scores in 1993 compared to 1992 were lower ratings for DO (fair at two locations and poor at one);
lower ratings for the fish assemblage (poor at two locations and fair at one); and addition of ratings
for the benthic macro invertebrates (fair at two locations and poor at one). The ecological health
indicator with the best rating in 1993 was chlorophyll, which rated good at the forebay.
The DO problem at the forebay and mid-reservoir site on the South Fork Holston River
arm is different than other tributary, storage reservoirs. The typical problem is hypolimnetic anoxia,
which is the case at the Watagua River mid-reservoir site. At the other two Boone Reservoir sites,
the DO problem occurs in the middle stratum of the water column (metal imnion) due to oxygen
demand of local sewage treatment plant discharges.
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Reservoir Use Suitability
Studies conducted by the state of Tennessee found PCBs and chlordane in fish tissue,
resulting in a state-issued advisory that catfish and carp should not be eaten by children, pregnant
women, and nursing mothers. Further, all other people should limit their consumption of these
particular fish. Additional fish samples were collected by TVA in autumn 1993, but results were not
available at the time this report was prepared.
Bacteriological sampling was conducted at two swimming areas and four boat ramps in
1993. The geometric mean concentrations of fecal coliform bacteria were well within Tennessee's
criteria for recreation, although one sample at the Boone Dam swimming area was high.
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17.4 South Holston Reservoir
Physical Description
South Holston Reservoir in northeastern Tennessee and southwestern Virginia is created by
South Holston Dam, located on the South Fork of the Holston River at mile 49.8. The dam creates a
storage pool approximately 24 miles long, over 230 feet deep near the dam, with an average depth of
86.5 feet and approximately 7600 acres in surface area. With an average annual discharge of about
980 cfs from the dam, the average hydraulic residence time is almost one year (340 days)-one of the
longest residence times of any TVA reservoir. Average annual drawdown of South Holston Reservoir
is about 33 feet.
Two locations are monitored for Vital Signs-the forebay and mid-reservoir. Sediment and
benthic macroinvertebrate sampling were added for the first time in 1993.
Ecological Health
The ecological health evaluation of South Holston Reservoir was fair (65 percent) in 1993,
slightly better than in 1992 (57 percent) and 1991 (60 percent). A consistent problem has been with
DO concentrations (as is the case with most deep storage impoundments), which rated poor at the
forebay and very poor at the mid-reservoir site in 1993. Despite the poor ratings for DO, conditions
were slightly improved at the forebay in 1993, compared to 1992. The ecological health indicator
primarily responsible for the higher overall reservoir rating in 1993 was sediment quality (rated good
at both sample sites). Sediments had not been sampled in previous years. Another indicator added in
1993, the benthic macroinvertebrate community, received a very poor rating at the forebay (with most
metrics receiving the lowest score possible) and a fair rating at the mid-reservoir sample site.
Interestingly, scores for the benthos do not parallel those for DO at the two sample sites, indicating
other factor(s) may be affecting benthic macroinvertebrates at the forebay. The fish assemblage rated
good at the forebay and fair at the mid-reservoir site.
Reservoir Use Suitability
There are no fish consumption advisories on South Holston Reservoir. The most recent
TVA data for fish tissue samples for fish collected in autumn 1991 found low or nondetectable
concentrations of all pesticides, PCBs, and metals (except mercury which was slightly elevated).
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17.5 Watauga Reservoir
Physical Description
Watauga Dam in the northeastern corner of Tennessee impounds the Watauga River at
mile 36.7. It forms a pool 16 miles in length, approximately 6400 acres in surface area, about 274
feet deep at the dam, and an average depth of about 89 feet, making it the second-deepest reservoir
sampled as part of TVA's Vital Signs Monitoring Program. With an annual average discharge of
about 700 cfs, Watauga Reservoir also has the longest hydraulic residence time of any of the Vital
Signs reservoirs (about 400 days). Average annual drawdown of Watauga Reservoir is about 26 feet.
Two locations are monitored on Watauga Reservoir, the forebay and mid-reservoir.
Sediment quality and benthic macroinvertebrates were examined for the first time in 1993.
Ecological Health
The overall ecological health for Watauga Reservoir was fair in 1993 (61 percent), about
the same as in 1992 (57 percent). The ecological health in both 1992 and 1993 rated lower than in
1991, although all three years fell within the fair range. Similar to previous years, chlorophyll rated
good at both sample sites in 1993. DO rated excellent at the forebay and fair at the mid-reservoir
sites in 1993, a slight improvement compared to 1992. The fish assemblage was poor at the forebay
in 1993 due to low abundance and diversity and rated fair at the mid-reservoir site, mostly due to low
abundance. The benthic macroinvertebrate community, not sampled in Watauga Reservoir prior to
1993, was very poor at both locations. The benthos community was among the poorest in all Vital
Signs reservoirs examined in 1993. This would not appear to be related to low DO concentrations;
instead, the poor sediment quality at the forebay (due to toxicity to test animals and high ammonia)
may have contributed to the poor benthos.
Reservoir Use Suitability
There are no fish consumption advisories on Watauga Reservoir. The most recent fish
tissue collections by TVA were made in autumn 1991. All pesticides, PCBs, and metals (except
mercury which was sightly elevated) were low or not detected.
Fecal coliform bacteria concentrations were very low at all five sites tested in 1993, which
included one designated and an informal swimming area.
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17.6 Holston River Stream Monitoring Site
Physical Description
The TVA stream monitoring station on the Holston River is located near Church Hill,
Tennessee. The Holston River basin above this location is 2819 square miles or 74 percent of the
entire Holston River basin. Two major tributaries, the North Fork Holston River (729 square miles)
and the South Fork Holston River (2048 square miles), meet above Church Hill to form the Holston
River. Principal tributaries to the South Fork Holston River include the Watauga River (869 square
miles) and the Middle Fork Holston River (244 square miles). Two notable tributaries to the
Watauga River include the Doe River (137 square miles) and Roan Creek (167 square miles).
There are five reservoirs in the basin. Fort Patrick Henry Dam and Boone Dam impound
the lower South Fork Holston River. The South Fork Holston Dam impounds the upper South Fork
Holston River and the Middle Fork Holston River. Wilbur Dam and Watauga Dam impound the
Watauga River.
Although most of the basin land use is agricultural or forestry, several urban areas
(Kingsport, Johnson City, and Elizabethton, Tennessee, and Marion and Abingdon, Virginia) are
within the basin.
Ecological Health
The overall ecological health of the Holston River at this site was fair for 1993 as in 1992. Sediment
quality improved from fair to good, and the fish community showed a slight improvement over 1992.
Bottom-dwelling animals and nutrient ratings remain unchanged.
Use Suitability
Seven sites between Fort Patrick Henry Reservoir and South Holston Dam were tested for
fecal coliform bacteria in 1993. South Fork Holston River met bacteriological water quality criteria
for water contact recreation, and was only slightly impacted by the two tributaries tested. Thomas
and Beidleman Creeks did not meet criteria.
A five fish composite each of carp, channel catfish, and largemouth bass were collected
during summer 1992 and analyzed for selected metals, pesticides, and PCBs. AH analytes were not
detected or found in low concentrations except slightly elevated levels of mercury in largemouth
(0.5 ng/g), PCBs in carp (0.6 jig/g), and chlordane in channel catfish (0.08 /xg/g).
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REFERENCES
Individual Technical Reports for Monitoring - 1993
Carroll, T.L., J.P. Fehring, and D.L. Meinert, 1994. "Tennessee Valley Reservoir and Stream
Quality, 1993 - Physical and Chemical Characteristics of Water, Reservoir Vital Signs
Monitoring" TVA, Water Management, Chattanooga, Tennessee (in preparation).
Fehring, J.P. 1994. "Tennessee Valley Reservoir and Stream Quality, 1993 - Bacteriological
Conditions in the Tennessee Valley." TVA Water Management, Clean Water Initiative,
Chattanooga, Tennessee (in preparation).
Hickman, G.D., A.M. Brown, and G. Peck, 1994. "Tennessee Valley Reservoir and Stream Quality,
1993-Summary of Reservoir Fish Assemblage Results." TVA, Water Management, Norris,
Tennessee.
Moses, J., D. Simbeck, and D. Wade. 1994. "Acute Toxicity Screening of Reservoir Water and
Sediment Using Daphnids (Ceriodaphnia dubia") and Rotifers [Rotox™], Reservoir Vital Signs
Monitoring, Summer 1993." TVA Water Management, (in preparation).
Moses, J., D. Simbeck, and D. Wade. 1994b. "Acute Toxicity Screening of Stream Water and
Sediment Using Daphnids ("Ceriodaphnia dubia) and Rotifers [Rotox™], Stream Vital Signs
Monitoring, Summer 1993." TVA Water Management (in preparation).
Strunk, J.W., 1993. "Fixed-Station Monitoring Network, A Summary of Physical, Chemical, and
Biological Characteristics, Water Years 1990-1993." TVA, Water Management, Chattanooga,
Tennessee (in preparation).
Tennessee Valley Authority, 1994. River Pulse: A Report on the Condition of the Tennessee River
and its Tributaries in 1993. TVA, Water Management, Chattanooga, Tennessee.
Masters, A.E., and A.K. Wales, 1994. "Tennessee Valley Reservoir and Stream Quality, 1993 -
Benthic Macroinvertebrate Community Results, Reservoir Vital Signs Monitoring." TVA, Water
Management, Chattanooga, Tennessee.
Individual Technical Reports for Monitoring - 1992
Brown, A.M., G.D. Jenkins, and G.D. Hickman, 1993. "Reservoir Monitoring, 1992 - Summary of
Fish Community Results." TVA, Water Resources, Norris, Tennessee.
Burns, E.R., A.L. Bates, and D.H. Webb, 1993. "Aquatic Plant Management Program - Current
Status and Seasonal Workplan - 1993." TVA, Water Resources, Vector and Plant Management
Program. Muscle Shoals, Alabama.
-191-
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Dycus, D.L., and D.L. Meinert, 1993. "Reservoir Monitoring - Monitoring and Evaluation of
Aquatic Resources Health and Use Suitability in Tennessee Valley Authority Reservoirs."
TVA/WM-93/15, TVA, Water Management, Chattanooga, Tennessee.
Fehring, J.P., 1993. "Reservoir Monitoring, 1992 - Bacteriological Conditions in the Tennessee
Valley." TVA/WM—93/11, TVA, Water Resources, Chattanooga, Tennessee.
Fehring, J.P., and D.L. Meinert, 1993. "Reservoir Vital Signs Monitoring, 1992 - Physical and
Chemical Characteristics of Water and Sediment." TVA, Water Resources, Chattanooga,
Tennessee.
Masters, A.E., 1993. "Reservoir Monitoring, 1992 - Benthic Macroinvertebrate Community Results."
TVA, Water Management, Chattanooga, Tennessee.
Moses, J., T.C. Sesler, D.C. Wade, and D.L. Meinert, 1993. "Reservoir Monitoring, 1992 - Acute
Toxicity Screening of Reservoir Water and Sediment Using Rotifers [Rotox™] and Light Emitting
Bacteria [Microtox™]." TVA, Water Management, Muscle Shoals, Alabama.
Moses, J., T.C. Sesler, and D.C. Wade, 1993. "Short-Term Chronic and Acute Toxicity Screening
of Water and Sediment Using Fathead Minnows, Daphnids, Rotifers [Rotox™], and Light Emitting
Bacteria [Microtox™], Ambient Stream Monitoring, Summer of 1992." TVA, Water Management,
Muscle Shoals, Alabama.
Tennessee Valley Authority, 1993. "Reservoir Monitoring - 1992, Summary of Vital Signs and Use
Suitability Monitoring on Tennessee Valley Reservoirs." TVA, Water Management, Chattanooga,
Tennessee.
Tennessee Valley Authority, 1993. River Pulse: A Report on the Condition of the Tennessee River
and its Tributaries in 1992. TVA, Water Management, Chattanooga, Tennessee.
Williams, D.L., and D.L. Dycus. 1993. "Reservoir Monitoring, 1992 - Results of Fish Tissue
Studies in the Tennessee Valley in 1991 and 1992." TVA, Water Management, Chattanooga,
Tennessee.
Individual Technical Reports for Monitoring - 1991
Bates, J.A., G.E. Hall, and D.L. Dycus, 1992. "Reservoir Monitoring, 1991 - Fish Tissue Studies in
the Tennessee Valley in 1990." TVA/WR—92/7, TVA, Water Resources, Chattanooga,
Tennessee.
Burns, E.R., A.L. Bates, and D.H. Webb, 1992. "Aquatic Plant Management Program - Current
Status and Seasonal Workplan - 1992." TVA, Water Resources, Vector and Plant Management
Program. Muscle Shoals, Alabama.
Fehring, J.P., 1992. "Reservoir Monitoring, 1991 - Bacteriological Conditions in the Tennessee
Valley." TVA/WR-92/6, TVA, Water Resources, Chattanooga, Tennessee.
-192-
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Masters, A.E., 1992. "Reservoir Vital Signs Monitoring, 1991 - Benthic Macroinvertebrate
Community Results." TVA/WR-92/3, TVA, Water Resources, Chattanooga, Tennessee.
Meinert, D.L., and J.P. Fehring, 1992. "Reservoir Vital Signs Monitoring, 1991 - Physical and
Chemical Characteristics of Water and Sediment." TVA/WR—92/1, TVA, Water Resources,
Chattanooga, Tennessee.
Moses, J., and D.C. Wade, 1992. "Reservoir Vital Signs Monitoring, 1991 - Acute Toxicity
Screening of Reservoir Water and Sediment." TVA/WR-92/2, TVA, Water Resources.
Parr, K.P., 1991. "Water Quality of the TVA Fixed-Station Monitoring Network (1986-1989)."
TVA/WR/WQ—91/3, TVA, Water Resources.
Scott, E.M., G.D. Hickman, and A.M. Brown, 1992. "Reservoir Vital Signs Monitoring, 1991 - Fish
Community Results." TVA/WR-92/5, TVA, Water Resources.
Tennessee Valley Authority, 1992. "Reservoir Vital Signs Monitoring: 1991, Summary of Vital Signs
and Use Impairment Monitoring on Tennessee Valley Reservoirs." TVA/WR-92/8, TVA, Water
Resources, Chattanooga, Tennessee.
Tennessee Valley Authority, 1992a. River Pulse: A Report on the Condition of the Tennessee River
and its Tributaries in 1991. TVA, Water Resources, Chattanooga, Tennessee.
Wilson, W.K., 1992. "Reservoir Vital Signs Monitoring, 1991 - Hydroacoustic Estimates of Fish
Abundance." TVA/WR-92/4, TVA, Water Resources.
Individual Technical Reports for Monitoring - 1990
Dycus, D.L., and D.L. Meinert. "Reservoir Monitoring, 1990 - Summary of Vital Signs and Use
Impairment Monitoring on Tennessee Valley Reservoirs." TVA/WR—91/1, TVA, Water
Resources, Chattanooga, Tennessee.
Fehring, J.P., 1991. "Reservoir Monitoring, 1990 Bacteriological Conditions in the Tennessee
Valley." TVA/WR/WQ-91/11, TVA, Water Resources, Chattanooga, Tennessee.
Hall, G.E., and D.L. Dycus, 1991. "Reservoir Monitoring, 1989 - Fish Tissue Studies in the
Tennessee Valley." TVA/WR/AB—91/12, TVA, Water Resources, Chattanooga, Tennessee.
Hickman, G.D., E.M. Scott, and A.M. Brown, 1991. "Reservoir Vital Signs Monitoring, 1990 - Fish
Community Results." TVA/WR/AB— 91/3, TVA, Water Resources.
Jenkinson, J.J., 1991. "Reservoir Vital Signs Monitoring, 1990 - Benthic Macroinvertebrate
Community Results 1990." TVA/WR/AB- 91/6, TVA, Water Resources, Chattanooga,
Tennessee.
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Meinert, D.L., 1991. "Reservoir Vital Signs Monitoring, 1990 - Physical and Chemical
Characteristics of Water and Sediment." TVA/WR/WQ—91/10, TVA, Water Resources,
Chattanooga, Tennessee.
Moses, J., and D.C. Wade, 1991. "Reservoir Vital Signs Monitoring, 1990 - Acute Toxicity
Screening of Reservoir Water and Sediment." TVA/WR/AB-91/2, TVA, Water Resources.
Saylor, C.F., and S.A. Ahlstedt, 1990. "Application of Index of Biotic Integrity (IBI) to
Fixed-Station Water Quality Monitoring Sites." TVA/WR/AB-90/12, TVA, Water Resources,
Norris, Tennessee, September 1990.
Tennessee Valley Authority, 1991. "Reservoir Vital Signs Monitoring: 1990, Summary of Vital
Signs and Use Impairment Monitoring on Tennessee Valley Reservoirs." TVA, Water Resources,
Chattanooga, Tennessee.
Wilson, W. K., 1991. "Reservoir Vital Signs Monitoring, 1990 - Hydroacoustic Estimates of Fish
Abundance 1990." TVA/WR/AB- 91/3, TVA, Water Resources.
Other References
Burns, E.R., A. L. Bates, and D. H. Webb. 1994. "Aquatic Plant Management Program-Current
Status and Seasonal Workplan - 1994." TVA Water Management, Clean Water Initiative, Muscle
Shoals, Alabama (in preparation).
Carlson, R.E., 1977. "A Trophic State Index for Lakes." Limnology and Oceanography. 22:361-369.
Environmental Protection Agency, 1992. Sediment Classification Methods Compendium. EPA
823-R-92-006, USEPA, Washington, D.C.
Environmental Protection Agency, 1991. "Guidelines for the Preparation of the 1992 State Water
Quality Assessments (305(b) Reports)." USEPA, Washington, D.C.
Environmental Protection Agency, 1986. "Quality Criteria for Water - 1986." EPA-440/5-86-001.
Environmental Protection Agency, 1977. "Guidelines for the Pollutional Classification of Great Lakes
Harbor Sediments." USEPA, Region V, Chicago.
Hauser, G.E., M.D. Bender, M.C. Shiao, and R.T. Brown, 1987. "Two-Dimensional Modeling of
Water Quality in Cherokee Reservoir." WR28-1-590-131, TVA, Division of Air and Water
Resources.
Hutchinson, G. Evelyn, 1975. A Treatise on Limnology. Volume 1, Part 2 - Chemistry of Lakes,
J. Wiley and Sons, New York.
Iwanski, M.L., 1978. "Water Quality in Cherokee Reservoir." TVA, Water Quality and Ecology
Branch.
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Iwanski, M.L., J.M. Higgins, B.R. Kim, and R.C. Young, 1980. "Factors Affecting Water Quality
in Cherokee Reservoir." TVA, Division of Water Resources.
Karr, J.R., 1981. "Assessment of Biotic Integrity Using Fish Communities." Fisheries 6(6),
pp. 21-27.
Kerans, B.L., J.R. Karr, and S.A. Ahlstedt. 1992. "Aquatic Invertebrate Assemblages: Spatial and
Temporal Differences Among Sampling Protocols." Journal of the North American Benthological
Society, 1992, 11(4):377-390.
Masters, A., and T.A. McDonough, April 1993. TVA Water Management, Chattanooga, Tennessee,
Personal Communication.
SAS, 1989. SAS/STAT User's Guide. Version 6, 4th Edition, Volume 1, Cary, North Carolina,
p. 943.
Tennessee Valley Authority, 1992b. "Aquatic Research Laboratory Quality Assurance Program and
Standard Operating Procedures Manual." TVA, Division of Water Resources.
Tennessee Valley Authority, 1994. "Summarized Hydrologic Information, Tennessee River Basin -
1993 " jvA, Hydrologic Data Management, Systems Engineering, Knoxville, Tennessee.
U.S. Department of Commerce (USDOC), 1993. "Summarized Climatic Information, Tennessee
Valley Region - 1993." National Climatic Data Center, Asheville, North Carolina.
-195-
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TABLE OF CONTENTS—VOLUME II
INTRODUCTION 1
Vital Signs Monitoring 1
Use Suitability Monitoring 2
Bacteriological Studies 2
Fish Tissue Studies 2
KENTUCKY RESERVOIR WATERSHED 5
Kentucky Reservoir 7
Summary of 1993 Conditions - Ecological Health 7
Summary of 1993 Conditions - Use Suitability 10
Beech Reservoir 11
Summary of 1993 Conditions - Ecological Conditions 11
Summary of 1993 Conditions - Use Suitability 12
DUCK RIVER WATERSHED 13
Normandy Reservoir 15
Summary of 1993 Conditions - Ecological Health 15
Summary of 1993 Conditions - Use Suitability 16
Duck River Stream Monitoring Site 17
Summary of 1993 Conditions - Ecological Health 17
Summary of 1993 Conditions - Use Suitability 18
PICKWICK RESERVOIR - WILSON RESERVOIR WATERSHED 19
Pickwick Reservoir 21
Summary of 1993 Conditions - Ecological Health 21
Summary of 1993 Conditions - Use Suitability 23
Wilson Reservoir 25
Summary of 1993 Conditions - Ecological Health 25
Summary of 1993 Conditions - Use Suitability 27
Bear Creek Reservoir 29
Summary of 1993 Conditions - Ecological Health 29
Summary of 1993 Conditions - Use Suitability 30
Little Bear Creek Reservoir 31
Summary of 1993 Conditions - Ecological Health 31
Summary of 1993 Conditions - Use Suitability 32
Cedar Creek Reservoir 33
Summary of 1993 Conditions - Ecological Health 33
Summary of 1993 Conditions - Use Suitability 34
Bear Creek Stream Monitoring Site 35
Summary of 1993 conditions - Ecological Health 35
Summary of 1993 conditions - Use Suitability 36
197
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WHEELER RESERVOIR - ELK RIVER WATERSHED 37
Wheeler Reservoir 39
Summary of 1993 Conditions - Ecological Health 39
Summary of 1993 Conditions - Use Suitability 43
Tims Ford Reservoir 45
Summary of 1993 Conditions - Ecological Health 45
Summary of 1993 Conditions - Use Suitability 46
Elk River Stream Monitoring Site 49
Summary of 1993 Conditions - Ecological Health 49
Summary of 1993 Conditions - Use Suitability 49
GUNTERSVILLE RESERVOIR - SEQUATCHIE RIVER WATERSHED 51
Guntersville Reservoir 53
Summary of 1993 Conditions - Ecological Health 53
Summary of 1993 Conditions - Use Suitability 55
Sequatchie River Stream Monitoring Site 57
Summary of 1993 Conditions - Ecological Health 57
Summary of 1993 Conditions - Use Suitability 58
NICKAJACK RESERVOIR - CHICKAMAUGA RESERVOIR WATERSHED 59
Nickajack Reservoir 61
Summary of 1993 Conditions - Ecological Health 61
Summary of 1993 Conditions - Use Suitability 62
Chickamauga Reservoir 65
Summary of 1993 Conditions - Ecological Health 65
Summary of 1993 Conditions - Use Suitability 68
HIWASSEE RIVER WATERSHED 69
Hiwassee Reservoir 71
Summary of 1993 Conditions - Ecological Health 71
Summary of 1993 Conditions - Use Suitability 72
Chatuge Reservoir 73
Summary of 1993 Conditions - Ecological Health 73
Summary of 1993 Conditions - Use Suitability 74
Nottely Reservoir 75
Summary of 1993 Conditions - Ecological Health 75
Summary of 1993 Conditions - Use Suitability 76
Blue Ridge Reservoir 77
Summary of 1993 Conditions - Ecological Health 77
Summary of 1993 Conditions - Use Suitability 78
Ocoee Reservoir No. 1 (Parksville Reservoir) 79
Summary of 1993 Conditions - Ecological Health 79
Summary of 1993 Conditions - Use Suitability 80
198
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Hiwassee River Stream Monitoring Site 81
Summary of 1993 Conditions - Ecological Health 81
Summary of 1993 Conditions - Use Suitability 81
WATTS BAR RESERVOIR, FORT LOUDOUN RESERVOIR,AND MELTON
HILL RESERVOIR WATERSHED 83
Watts Bar Reservoir 85
Summary of 1993 Conditions - Ecological Health 85
Summary of 1993 Conditions - Use Suitability 87
Fort Loudoun Reservoir 89
Summary of 1993 Conditions - Ecological Health 89
Summary of 1993 Conditions - Use Suitability 91
Melton Hill Reservoir 93
Summary of 1993 Conditions - Ecological Health 93
Summary of 1993 Conditions - Use Suitability 95
Emory River Stream Monitoring Site 97
Summary of 1993 Conditions - Ecological Health 97
Summary of 1993 Conditions - Use Suitability 98
CLINCH RIVER AND POWELL RIVER WATERSHED 99
Norris Reservoir 101
Summary of 1993 Conditions - Ecological Health 101
Summary of 1993 Conditions - Use Suitability 103
Clinch River Stream Monitoring Site 105
Summary of 1993 Conditions - Ecological Health 105
Summary of 1993 Conditions - Use Suitability 105
Powell River Stream Monitoring Site 107
Summary of 1993 Conditions - Ecological Health 107
Summary of 1993 Conditions - Use Suitability 107
LITTLE TENNESSEE RIVER WATERSHED 109
Tellico Reservoir Ill
Summary of 1993 Conditions - Ecological Health 111
Summary of 1993 Conditions - Use Suitability 113
Fontana Reservoir 115
Summary of Conditions in 1993 - Ecological Health 115
Summary of Conditions in 1993 - Use Suitability 116
Little Tennessee River Stream Monitoring Site 119
Summary of 1993 Conditions - Ecological Health 119
Summary of 1993 Conditions - Use Suitability 119
FRENCH BROAD RIVER WATERSHED 121
Douglas Reservoir 123
Summary of 1993 Conditions - Ecological Health 123
Summary of Conditions in 1993 - Use Suitability 124
199
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French Broad River Stream Monitoring Site 127
Summary of 1993 Conditions - Ecological Health 127
Summary of 1993 Conditions - Use Suitability 128
Nolichucky River Stream Monitoring Site 129
Summary of 1993 Conditions - Ecological Health 129
Summary of 1993 Conditions - Use Suitability 130
HOLSTON RIVER WATERSHED 131
Cherokee Reservoir 133
Summary of 1993 Conditions - Ecological Health 133
Summary of Conditions in 1993 - Use Suitability 134
Fort Patrick Henry Reservoir 137
Summary of Conditions in 1993 - Ecological Health 137
Summary of Conditions in 1993 - Use Suitability 138
Boone Reservoir 139
Summary of Conditions in 1993 - Ecological Health 139
Summary of Conditions in 1993 - Use Suitability 141
South Holston Reservoir 143
Summary of Conditions in 1993 - Ecological Health 143
Summary of Conditions in 1993 - Use Suitability 144
Watauga Reservoir 145
Summary of Conditions in 1993 - Ecological Health 145
Summary of Conditions in 1993 - Use Suitability 146
Holston River Stream Monitoring Site 147
Summary of 1993 Conditions - Ecological Health 147
Summary of 1993 Conditions - Use Suitability 148
CONTENTS FOR VOLUME I 149
KEY CONTACTS FOR MONITORING FUNCTIONS 152
200
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Tennessee
Valley
Authority
TENNESSEE VALLEY RESERVOIR AND STREAM QUALITY -1993
SUMMARY OF VITAL SIGNS AND USE SUITABILITY MONITORING
VOLUME II
CLEAN WATER
~ A
INITIATIVE
«r \fntryC&> 3.
Water Management May 1994
Chattanooga, Tennessee
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TENNESSEE VALLEY AUTHORITY
Resource Group
Water Management
TENNESSEE VALLEY RESERVOIR AND STREAM QUALITY - 1993
SUMMARY OF VITAL SIGNS AND
USE SUITABILITY MONITORING
Volume II
Report Coordinators:
Donald L. Dycus
and
Dennis L. Meinert
Authors and Contributors:
Steven A. Ahlstedt
Allen M. Brown
Neil C. Carriker
Tammy L. Carroll
Donald L. Dycus
Joe P. Fehring
Gary D. Hickman
Dennis L. Meinert
Charles F. Say lor
Damien J. Simbeck
Janis W. Strunk
Amy K. Wales
David H. Webb
Chattanooga, Tennessee
May 1994
-------
TABLE OF CONTENTS
INTRODUCTION 1
Vital Signs Monitoring 1
Use Suitability Monitoring 2
Bacteriological Studies 2
Fish Tissue Studies 2
KENTUCKY RESERVOIR WATERSHED 5
Kentucky Reservoir 7
Summary of 1993 Conditions - Ecological Health 7
Summary of 1993 Conditions - Use Suitability 10
Beech Reservoir 11
Summary of 1993 Conditions - Ecological Conditions 11
Summary of 1993 Conditions - Use Suitability 12
DUCK RIVER WATERSHED 13
Normandy Reservoir 15
Summary of 1993 Conditions - Ecological Health 15
Summary of 1993 Conditions - Use Suitability 16
Duck River Stream Monitoring Site 17
Summary of 1993 Conditions - Ecological Health 17
Summary of 1993 Conditions - Use Suitability 18
PICKWICK RESERVOIR - WILSON RESERVOIR WATERSHED 19
Pickwick Reservoir 21
Summary of 1993 Conditions - Ecological Health 21
Summary of 1993 Conditions - Use Suitability 23
Wilson Reservoir 25
Summary of 1993 Conditions - Ecological Health 25
Summary of 1993 Conditions - Use Suitability 27
Bear Creek Reservoir 29
Summary of 1993 Conditions - Ecological Health 29
Summary of 1993 Conditions - Use Suitability 30
Little Bear Creek Reservoir 31
Summary of 1993 Conditions - Ecological Health 31
Summary of 1993 Conditions - Use Suitability 32
Cedar Creek Reservoir 33
Summary of 1993 Conditions - Ecological Health 33
Summary of 1993 Conditions - Use Suitability 34
Bear Creek Stream Monitoring Site 35
Summary of 1993 conditions - Ecological Health 35
Summary of 1993 conditions - Use Suitability 36
111
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WHEELER RESERVOIR - ELK RIVER WATERSHED 37
Wheeler Reservoir 39
Summary of 1993 Conditions - Ecological Health 39
Summary of 1993 Conditions - Use Suitability 43
Tims Ford Reservoir 45
Summary of 1993 Conditions - Ecological Health 45
Summary of 1993 Conditions - Use Suitability 46
Elk River Stream Monitoring Site 49
Summary of 1993 Conditions - Ecological Health 49
Summary of 1993 Conditions - Use Suitability 49
GUNTERSVILLE RESERVOIR - SEQUATCHIE RIVER WATERSHED 51
Guntersville Reservoir 53
Summary of 1993 Conditions - Ecological Health 53
Summary of 1993 Conditions - Use Suitability 55
Sequatchie River Stream Monitoring Site 57
Summary of 1993 Conditions - Ecological Health 57
Summar>' of 1993 Conditions - Use Suitability 58
NICKAJACK RESERVOIR - CHICKAMAUGA RESERVOIR WATERSHED 59
Nickajack Reservoir 61
Summary' of 1993 Conditions - Ecological Health 61
Summary of 1993 Conditions - Use Suitability 62
Chickamauga Reservoir 65
Summary' of 1993 Conditions - Ecological Health 65
Summary of 1993 Conditions - Use Suitability 68
H1WASSEE RIVER WATERSHED 69
Hiwassec Reservoir 71
Summary' of 1993 Conditions - Ecological Health 71
Summary of 1993 Conditions - Use Suitability 72
Chatuge Reservoir 73
Summary of 1993 Conditions - Ecological Health 73
Summary of 1993 Conditions - Use Suitability 74
Nottcly Reservoir 75
Summary of 1993 Conditions - Ecological Health 75
Summary of 1993 Conditions - Use Suitability 76
Blue Ridge Reservoir 77
Summary' of 1993 Conditions - Ecological Health 77
Summary of 1993 Conditions - Use Suitability 78
Ocoee Reservoir No. 1 (Parksville Reservoir) 79
Summary of 1993 Conditions - Ecological Health 79
Summary of 1993 Conditions - Use Suitability 80
IV
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Hiwassee River Stream Monitoring Site 81
Summary of 1993 Conditions - Ecological Health 81
Summary of 1993 Conditions - Use Suitability 81
WATTS BAR RESERVOIR, FORT LOUDOUN RESERVOIR,AND MELTON HILL
RESERVOIR WATERSHED 83
Watts Bar Reservoir 85
Summary of 1993 Conditions - Ecological Health 85
Summary of 1993 Conditions - Use Suitability 87
Fort Loudoun Reservoir 89
Summary of 1993 Conditions - Ecological Health 89
Summary of 1993 Conditions - Use Suitability 91
Melton Hill Reservoir 93
Summary of 1993 Conditions - Ecological Health 93
Summary of 1993 Conditions - Use Suitability 95
Emory River Stream Monitoring Site 97
Summary of 1993 Conditions - Ecological Health 97
Summary of 1993 Conditions - Use Suitability 98
CLINCH RIVER AND POWELL RIVER WATERSHED 99
Norris Reservoir 101
Summary of 1993 Conditions - Ecological Health 101
Summary of 1993 Conditions - Use Suitability 103
Clinch River Stream Monitoring Site 105
Summary of 1993 Conditions - Ecological Health 105
Summary of 1993 Conditions - Use Suitability 105
Powell River Stream Monitoring Site 107
Summary of 1993 Conditions - Ecological Health 107
Summary of 1993 Conditions - Use Suitability 107
LITTLE TENNESSEE RIVER WATERSHED 109
Tellico Reservoir Ill
Summary of 1993 Conditions - Ecological Health Ill
Summary of 1993 Conditions - Use Suitability 113
Fontana Reservoir 115
Summary of Conditions in 1993 - Ecological Health 115
Summary of Conditions in 1993 - Use Suitability 116
Little Tennessee River Stream Monitoring Site 119
Summary of 1993 Conditions - Ecological Health 119
Summary of 1993 Conditions - Use Suitability 119
FRENCH BROAD RIVER WATERSHED 121
Douglas Reservoir 123
Summary of 1993 Conditions - Ecological Health 123
Summary of Conditions in 1993 - Use Suitability 124
v
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French Broad River Stream Monitoring Site 127
Summary of 1993 Conditions - Ecological Health 127
Summary of 1993 Conditions - Use Suitability 128
Nolichucky River Stream Monitoring Site 129
Summary of 1993 Conditions - Ecological Health 129
Summary of 1993 Conditions - Use Suitability 130
HOLSTON RIVER WATERSHED 131
Cherokee Reservoir 133
Summary of 1993 Conditions - Ecological Health 133
Summary of Conditions in 1993 - Use Suitability 134
Fort Patrick Henry Reservoir 137
Summary of Conditions in 1993 - Ecological Health 137
Summary of Conditions in 1993 - Use Suitability 138
Boone Reservoir 139
Summary of Conditions in 1993 - Ecological Health 139
Summary of Conditions in 1993 - Use Suitability 141
South Holston Reservoir 143
Summary of Conditions in 1993 - Ecological Health 143
Summary of Conditions in 1993 - Use Suitability 144
Watauga Reservoir 145
Summary of Conditions in 1993 - Ecological Health 145
Summary of Conditions in 1993 - Use Suitability 146
Holston River Stream Monitoring Site ; 147
Summary of 1993 Conditions - Ecological Health 147
Summary of 1993 Conditions - Use Suitability 148
CONTENTS FOR VOLUME 1 149
KEY CONTACTS FOR MONITORING FUNCTIONS 152
VI
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INTRODUCTION
The Tennessee Valley Authority (TVA) initiated a systematic, Valley-wide water quality and
aquatic ecological monitoring program in 1986. The program started with a stream component and a
reservoir component was added in 1990. The two primary objectives of these monitoring efforts are to
evaluate the ecological health (Vital Signs Monitoring) of major streams and reservoirs in the Tennessee
Valley and to examine how well these water resources meet the swimmable and fishable goals of the Clean
Water Act (Use Suitability Monitoring).
Vital Signs Monitoring
Stream monitoring has been conducted on 12 large tributaries since 1986. Beginning in 1994, six
additional tributaries will be monitored; all with watersheds of at least 500 square miles. Reservoir
monitoring started with 12 reservoirs (mostly mainstream reservoirs) in 1990 and has expanded
progressively to the full complement of 30 reservoirs in 1993. No further expansion of either stream or
reservoir monitoring is planned. This report summarizes results of these monitoring efforts in 1993.
Volume I is the main body of the report and Volume II is a data summary by sampling location within
watershed areas.
Until 1991, the ecological health evaluations were based on subjective evaluation of the data. A
weight-or-evidcnce approach was used— a stream or reservoir was deemed healthy if most of the physical,
chemical, and biological components appeared healthy. Beginning with the 1991 results, a more
quantitative approach was developed that has been used the last three years. This approach integrates
information on important indicators of ecological health. For reservoirs, five indicators are used—
dissolved oxygen, chlorophyll a, sediment quality, benthic macroinvertebrates, and fishes. Stream
evaluations are similar except dissolved oxygen is not rated and nutrient concentrations are substituted for
chlorophyll a concentrations. For each indicator (or metric), scoring criteria are developed that assign a
score ranging form 1 to 5 representing very poor to excellent conditions. Scores for all indicators at a
location are summed. For streams and smaller reservoirs, only one site is monitored. For larger reservoirs,
multiple sites are monitored, and the overall reservoir score is achieved by totaling scores for all locations.
The resulting total is divided by the maximum possible score. Thus, the possible range of scores is from
20 percent (all metrics very poor) to 100 percent (all metrics excellent). Hence, an overall ecological health
rating of good, fair, or poor is obtained for each stream site or reservoir. A health rating border-line
between two of these categories is considered poor-fair or fair-good. Each year, the most recent
information is evaluated with the same basic approach, modified to incorporate improvements based on
comments from reviewers and additional data.
Stream monitoring results for 1993 indicated seven streams rated good (three of these with perfect
scores), three streams rated fair to good, and one stream rated poor Full evaluation was not possible for
one stream because only three of the four indicators were monitored in 1993 The only stream to receive a
poor rating was the French Broad River. This overall rating was caused by poor scores for nutrients and
fishes, a fair score for benthos, and a good score for sediment quality.
Reservoirs are stratified into two groups for evaluation: run-of -the-river reservoirs and deep
storage reservoirs. Separate scoring criteria are used for the two categories Overall ratings for the 11 run-
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of-the-river reservoirs in 1993 ranged from 58 to 88 percent. Four reservoirs rated good (74 to 88 percent),
three rated fair to good (71 to 73 percent), three rated fair (63 to 68 percent), and one rated poor to fair (58
percent) Overall ratings for the 19 storage reservoirs ranged from 52 to 72 percent. Two reservoirs rated
fair to good (both 72 percent), fourteen rated fair (58 to 67 percent), and three rated poor (52 to 56
percent).
Results did not yield any "big surprises"— most streams and reservoirs fell within expected
categories. Similar results were observed in both 1991 and 1992, primarily due to similar meteorological
conditions and reservoir flows during the period. Generally poorer ratings observed in storage reservoirs
were primarily because of low dissolved oxygen in the hypolimnion. This is an ecologically undesirable
condition that is mostly due to strong thermal stratification that occurs in deep reservoirs.
Use Suitability Monitoring
Use Suitability Monitoring provides screening level information on the suitability of selected areas
within TVA reservoirs for water contact activities (swimmable) as determined by bacteriological studies
and suitability of fish from TVA reservoirs for human consumption (fishable) as determined by fish tissue
studies
Bacteriological Studies
Bacteriological samples are collected at over 200 sites in the Tennessee Valley: designated
swimming areas, canoe access sites, highly used recreational areas, and selected non-recreation sites that
provide information on pollution sources or inflow stream quality. Not all sites are sampled each year.
Beginning in 1993, each recreation site will be revisited at least every other year.
In 1993, bacteriological sampling at recreation sites was conducted at 71 swimming areas and 14
canoe access points. All but two swimming areas met the regulatory criterion to be considered safe. Even
those two sites met the criterion if samples collected after heavy rains were excluded. Four canoe access
points (all on the Duck River) exceeded the criterion, in dry or wet weather.
Bacteriological sampling at non-recreation areas was conducted at 35 sites in 1993. Only one
reservoir site and two stream sites failed to meet recreation criteria.
The results of studies summarized above are consistent with previous surveys. Fecal coliform
concentrations were generally lower in 1993 due to lower than normal summer rainfall. Bacteriological
water quality is most areas of TVA reservoirs is good. In streams it is much poorer, especially after
rainfall.
Fish Tissue Studies
Fish tissues studies examine fillets from important fish species for selected metals, pesticides, and
polychlorinated biphenyls (PCBs) on the U.S. Environmental Protection Agency's list of priority pollutants
Resulting data are provided to appropriate state agencies to determine the need for further study and
possible issuance of fish consumption advisories. Fish tissue data reported here represent autumn 1992
2
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collections Results for fish collected in autumn 1993 were not available at the time this report was
prepared due to the time required for laboratory analysis.
Results of screening studies in 1992 did not reveal any new areas in need of intensive
investigations. Concentrations of at least one contaminant were high enough to warrant sampling again at
the screening level in 1993. Results of intensive studies (i.e., in-depth studies where there are know or
suspected problems) did not indicate substantial changes from previous years
3
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KENTUCKY RESERVOIR WATERSHED
5
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Kentucky Reservoir
Summary of 1993 Conditions - Ecological Health
Water—During the summer of 1993 (April-September), the coolest surface water temperatures in
Kentucky Reservoir were in April and the warmest in July. Surface temperatures ranged from a minimum
of 13.6°C to a maximum of 31.5°C at the forebay; from 15.8°C to 31.6°C at the transition zone; and from
16.1°C to 30.9°C at the sampling location in Big Sandy embayment. The State of Tennessee's maximum
water temperature criteria for the protection of fish and aquatic life is 30.5°C.
Dissolved oxygen (DO) concentrations at the 1.5m depth ranged from a low of 6.2 mg/1 in July to a
high of 10.4 mg/1 in April at the forebay, from 5.8 mg/1 in August to 10.1 mg/1 in June at the transition
zone; and from 6.2 mg/1 in July to 10.3 mg/1 in April at the sampling location in Big Sandy embayment. At
the inflow sampling site (i.e. the tailrace of Pickwick Dam) a minimum DO of 4 .2 mg/1 was recorded in
July The State of Tennessee's minimum dissolved oxygen criteria for the protection of fish and aquatic life
is 5.0 mg/1, measured at the 1,5m depth.
The temperature and DO data depict a seasonal wanning and very weak thermal stratification of
Kentucky Reservoir in June-July 1993. The greatest surface-to-bottom temperature differential (AT) was
only about 3°C in June and July at the forebay and about 4'/2°C in Big Sandy embayment in June.
However, during July, a rather strong oxycline developed at Kentucky forebay and in the Big Sandy
embayment due to the drought like conditions and low flows through Kentucky Reservoir and the
Tennessee River system (see discussion in Section 4 0, Hydrologic Overview of 1993). In late July, forebay
dissolved oxygen ranged from surface concentrations of about 8-9 mg/l to bottom concentrations
approaching 0 mg/1. (The minimum DO observed in Kentucky Reservoir in 1993 was 0.1 mg/1 in July at
the bottom of the reservoir in the forebay.) Similar conditions were found in Big Sandy embayment,
although near bottom DO concentrations were never actually measured below 1 mg/1. The transition zone
DO concentrations were much more uniform and well mixed with the minimum bottom DO being 3 .6 mg/1
in July.
For the overall reservoir ecological health evaluation for Kentucky Reservoir, DO rated excellent at
the transition zone; good to excellent in Big Sandy embayment; and good at the forebay and inflow (i.e.,
Pickwick Dam tailrace). The good rating at the forebay would have rated higher had it not been for the
anoxic conditions which were found to exist for a short time (i.e. July) in the hypolimnion near Kentucky
dam. Likewise, the good rating at the inflow would also have been higher if oxygen levels had not fallen
below 5 mg/1 in the releases from Pickwick dam (i.e DO concentrations less than State of Tennessee's
5 mg/1 criteria, measured at the 1.5m depth).
In 1993, values of pH ranged from 6.7 to 9.2 on Kentucky Reservoir. Near surface values
exceeding 8.5 were observed at the forebay in July and in Big Sandy embayment in June and August. These
high pH's were coincident with high DO saturation values (exceeding 100 percent) and elevated chlorophyll
a concentrations, indicative of significant photosynthetic activity. The State of Tennessee's maximum pH
criteria for the protection of fish and aquatic life is 8.5.
Average total phosphorus (0.073 mg/1) and dissolved ortho phosphorus (0.029 mg/1)
concentrations at the transition zone were higher than at all other monitoring locations on the Tennessee
River, an effect of the upstream inflows from the Duck River with naturally high concentrations of
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phosphorus (median total phosphorus concentrations of about 0.24 mg/1). Total phosphorus concentrations
in the Tennessee River are approximately doubled by the inflows from the Duck River (annual mean daily
flow of approximately 4,100 cfs), and gradually decline downstream. The Duck River joins with the
Tennessee River at TRM 110.7, about 25 river miles upstream from the Kentucky Reservoir transition
zone sampling site. (For additional information see Section 5.0, Duck River Watershed.) Because of high
phosphorus concentrations, TN/TP ratios for samples collected at both the forebay and transition zone
were quite low ranging from 5 to 13, indicating very little nutrient limitation and conditions highly
supportive of primary productivity.
Chlorophyll a concentrations averaged 10.4 fag/1 at the forebay, 9.2 (ig/1 at the transition zone, and
18.0 jag/1 in Big Sandy embayment during the summer of 1993. In addition, high chlorophyll a
concentrations were measured in August (31 (ig/1) and September (35 jj.g/1) in Big Sandy embayment,
indicative of nuisance level algal blooms. [It is also interesting to note that the Big Sandy embayment had
among the highest organic nitrogen ( = 0.51 mg/1), organic carbon (= 4.2 mg/1), and color ( = 19 PCU)
concentrations measured at any Vital Signs reservoir monitoring location in 1993 ] Chlorophyll a values
which average greater than 10 (ig/1 are generally indicative of eutrophic conditions while values greater
than 15 jag/1 are often indicative of hyper-eutrophic conditions. Consequently, the chlorophyll a ratings
used in the 1993 ecological health evaluation for Kentucky Reservoir were fair at the forebay, good at the
transition zone, and poor in the Big Sandy embayment.
Sediment Quality—Chemical analyses of sediments in Kentucky Reservoir in 1993 did not reveal
any metal or organic analyte to be a concern in the two sample locations (i.e. forebay and transition zone)
in the main reservoir. However, high levels of un-ionized ammonia were measured (510 jag/I) in the Big
Sandy embayment. Toxicity tests detected no acute toxicity in the main reservoir, however, acute toxicity
to both daphnids (15 percent survival) and rotifers (20 percent survival) was detected in the Big Sandy
embayment. Particle size analysis showed sediments from the forebay and the Big Sandy embayment to be
almost entirely silt and clay (99 percent at each site), while those from the transition zone were 65 percent
silt and clay, 35 percent sand.
Sediment quality ratings used in the overall Kentucky Reservoir ecological health evaluation for
1993 were excellent at the forebay and transition zone, and poor in the Big Sandy embayment (due to the
presence of ammonia and toxicity to the test organisms).
Benthic Macroinvertebrates—The benthic communities were excellent in the forebay and
transition zone, fair in the inflow, and good in the Big Sandy embayment. The forebay had a total of 26
taxa with 1,658 organisms/m The dominant taxa at the forebay were Tubificidae (18%), Corbicula sp
(17 percent), and Musculium sp (17 percent). The transition zone represented a more diverse (33 taxa) but
less abundant (1,307 organisms/m ) community than the forebay with Tubificidae as the dominant taxa
(22 percent), followed closely by Hexagenia limbata (22 percent) The inflow site had 25 taxa and a total of
234 organisms/m with Cheumatopsvche sp (32 percent) and Corbicula sp (29 percent) as the dominant
taxa The Big Sandy embayment site had 20 taxa and 1,683 organisms/m with Chironomus sp
(37 percent), and Coelotanvpus tricolor (33 percent) as the principal taxa.
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The forebay and transition zone sites on Kentucky' Reservoir rated excellent primarily because of
the abundance of long-lived species such as Corbicula sp and Hexagenia sp, and because of a diverse and
balanced benthic community. The inflow rated only fair, in spite of an abundance of Corbicula sp, because
of reduced diversity and EPT (Ephemeroptera, Plecoptera, and Trichoptera) taxa. The Big Sandy
embayment received a good rating due to the diversity of organisms present and the evenness of dominant
organisms. An abundance of chironomids resulted in this site receiving a good rating instead of an excellent
rating.
Though not included in the overall health survey, the Kentucky tailwater benthic community was
also sampled. Diversity and a good EPT community, as well as low numbers of chironomids and tubificids,
allowed this site to obtain an excellent rating.
AquaticMacrophytes—Aquatic plants increased from 2,616 acres in 1992 to 3,465 acres in 1993.
Kentucky Reservoir had the third largest amount of aquatic vegetation within the TVA system. Aquatic
macrophytes peaked at about 7,100 acres in 1987. Significant declines in spinylcaf and southern naiad
populations have occurred in recent years. Eurasian watermilfoil was the dominant macrophyte on
Kentucky Reservoir and generally occurred in monospecific stands. However, it was sometimes mixed with
coontail and naiads. Aquatic vegetation on Kentucky Reservoir was primarily found from TRM 107
downstream to near the vicinity of Kentucky Dam.
Fish Assemblage—Fish data collection at near shore (45 electrofishing transects) and offshore
bottom areas (26 net-nights) showed a diverse fish assemblage of 46 species dominated in numbers by
gizzard shad (64 percent). Other abundant species included emerald shiners (5.6 percent), bluegill
(4.8 percent), and largemouth bass (2 percent). Electrofishing results indicated total numbers of fish were
approximately the same in the forebay (1,634) and transition zones (1,762) with considerably lower
numbers in the inflow zone (405) Gill netting fish abundance was also highest in the forebay (696) and
transition (494) areas Abundance at the inflow zone (69) was not comparable because of reduced effort.
Gizzard shad made up 36 percent of the total fish collected in gill net samples followed by yellow bass
(15.7 percent), skipjack herring (9.9 percent), and channel catfish (6.0 percent).
The Reservoir Fish Assemblage Index (RFAI) rated the littoral fish community (based on results of
electrofishing samples) fair in the forebay (RFAI=32), transition (RFAI=34), and inflow (RFAJ=40) zones
of Kentucky Reservoir The lower scores in transition and forebay zones were influenced by low numbers
of sucker species, a high percentage of tolerant species and omnivorous individuals, and high percentage of
dominance by a single species. The gill netting RFAI rated the transition zone excellent (RFAI=56) and the
forebay good (RFAI=42) Gill netting RFAI values were not calculated for inflow zones of run-of-the-river
reservoirs due to low numbers of replicate samples. The excellent score of 56 in the transition was the
highest ever observed and resulted from maximum scores in all metrics except number of sucker species
and percent tolerant species.
Combined electrofishing and gill netting RFAI scores for the forebay (RFAI=37) and the
electrofishing RFAI for the inflow (RFAI=40) were rated fair. The combined transition RFAI (RFAI=45)
ranked good exhibiting the second highest score of all run-of-the-river transition zones, due primarily to the
excellent gill netting results noted above.
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Combined fish samples in shoreline electrofishing (15 transects) and offshore gill netting (24 net-
nights) produced a total of 1,587 individuals including 27 species in the Big Sandy River embayment.
There were four times as many fish collected by electrofishing as gill netting, largely attributed to high
numbers of gizzard shad which made up 71 percent of the total sample.
The electrofishing RFAI score of 32 rated fair. The gill netting RFAI of 22 was the lowest
recorded for any of the embayment study sites in 1993, and resulted from minimum scores for eight of the
twelve metrics. The combined RFAI scores (RFAI=27) rated the Big Sandy embayment poor.
Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—Fourteen swimming beaches and one informal swimming area were
tested for fecal coliform bacteria in 1993. Bacteria concentrations were generally low at all 15 sites. The
highest geometric mean at any site was 47 colonies per 100 milliliters (47/100 ml), well below the
recreation criterion of 200/100 ml No site had more than one sample exceed 400/100 ml, so EPA's
guideline of no more than 10 percent of all samples exceeding 400/100 ml was also met. Two sites, Eva
Park and Greenhead Recreation Area, each had one sample exceed the Tennessee single sample criterion of
1,000/100 ml. The geometric mean of all samples at these two sites were 14 and 15/100 ml. The six
monthly Vital Signs samples collected at the forebay and transition zones were all at or below the detection
limit of 10/100 ml.
Fish Tissue—Channel catfish composites were collected in 1992 from generally the same locations
(except TRM 85 was sampled instead of TRM 100 to coincide with the transition zone location) as in
previous years. As in past years, concentrations of all analytes were low. One analyte of interest was lead
with a concentration of 0.6 |ag/g at TRM 85. Similar levels have occurred sporadically with no pattern in
locations over the five years screening samples have been collected from Kentucky Reservoir.
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Beech Reservoir
Summary of 1993 Conditions - Ecological Conditions
Water—Beech Reservoir is the smallest and shallowest of the monitored reservoirs. The average
flow through the reservoir in 1993 was only 64 percent of normal, making the average residence time over
600 days. The maximum temperature difference in the water column was 9.2°C in July, and had
disappeared by September. The maximum surface temperature was 29.7°C in July. The extent of the area
of depleted DO gave Beech Reservoir a poor DO rating for the reservoir ecological health index. DO
depletion (<1.0 mg/1) began at the bottom of the water column in May and expanded to within four meters
of the surface in June and July. As the reservoir destratificd the bottom waters became re-aerated, although
there was some low DO (2.2 mg/1) at the bottom in October.
Conductivities were generally in the 31 to 45 (imhos/cm range, but were much higher at the bottom
during times of DO depletion, reaching a maximum of 141 ^mhos/cm in August. Only in April and June
did pH exceed 8.0, and the maximum was only 8 3 The minimum pH was 6.6 and occurred at greater
depths during DO depletion.
Virtually all of the nitrogen was in the form of organic nitrogen Total nitrogen increased slightly
from 0.42 mg/1 in April to 0.51 mg/1 in August. Total and dissolved ortho phosphorus concentrations
dropped from 0.04 and 0.01 mg/1 in April to 0.02 and 0.002 mg/1 in August, respectively. The TN/TP ratio
thus increased from 11 to 26.5 from April to August. Secchi depths varied only from 1.0m in April and
September to 1.5m in May and June, the second lowest water clarity of the 19 tributary reservoir forebays
in 1993. Chlorophyll a concentrations were 3 jag/1 in April, 6 jag/1 in May, and varied from 9 to 14 jj.g/1 for
the rest of the sampling period. The average chlorophyll a concentration was 9 .0 jig/1, in the good range
(near the upper end) for the reservoir ecological health index. Total organic carbon dropped from 5.4 mg/1
in April to 3.3 mg/1 in August. Total phosphorus and total organic carbon concentrations were the second
lowest concentrations of the 19 tributary reservoir forebays in 1993.
Sediment—Chemical analyses of sediments in the forebay of Beech Reservoir in 1993 did not
reveal any metal or organic analvtc to be a concern. Toxicity tests detected no acute toxicity to the two
organisms tested; however, survival of daphnids (68 percent survival) was reduced. Particle size analysis
showed sediments in the forebay were 97 percent silt and clay.
Because of the slightly reduced survival of daphnids, the forebay sediment quality rating used in
the 1993 Beech Reservoir ecological health evaluation was good.
Benthic Macroinvertebrates—The forebay on Beech Reservoir supported a fair bcnthic
2
community. There were 24 taxa and 1,417 organisms/m , with Einfeldia sp (39 percent of the total) and
Chironomus sp (35 percent of the total) as the dominant species. This site had 2 metrics which rated good:
diversity and proportion of the sample composed of tubificids. Fair representations of EPT and long-lived
taxa were observed An abundance chironomids negatively impacted the benthic community rating.
Fish Assemblage—No fish assemblage information was collected in autumn 1993 because water
levels prevented access to the lake.
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Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—No bacteriological studies were conducted in 1993.
Fish Tissue—TVA has not conducted fish tissue studies on Beech Reservoir.
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DUCK RIVER WATERSHED
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Normandy Reservoir
Summary of 1993 Conditions - Ecological Health
Water—The average residence time in Normandy Reservoir was 201 days in 1993 as flows were
91 percent of normal. The maximum temperature difference in the water column was 23°C in July. The
maximum surface temperature was 32.3°C in July, the only month when the maximum temperature
exceeded 30.5°C, Tennessee's criteria for aquatic life. Metalimnetic and near-bottom oxygen depletion
began in June. By August, DO was below 0.1 mg/1 from the bottom to six meters from the surface. Surface
temperatures had cooled enough to mix with the metalimnion in October, increasing the depth of aerated
water to 10m The extent of the area of depleted DO gave Normandy a poor DO rating for the reservoir
ecological health index. Surface DO reached saturation levels of 120 percent or more on each sample date
from May through July.
Conductivities were about 100 jamhos/cm early in the year, began increasing at the bottom in June
and reached about 160 (imhos/cm in September and October. Normandy had slightly basic water (pH from
7.5 to 8.3) in April. Surface pH was over 9 from May through July, with a maximum pH of 9.5 in May.
Bottom pH dropped slightly during the summer to a minimum of 6.6 in September.
Total nitrogen concentration dropped from 0.72 mg/1 in April to 0.46 mg/1 in August. The decline
was due to the elimination of nitrates, 0.25 mg/1 in April and <0.01 mg/1 in August. Total phosphorus and
dissolved ortho-phosphorus concentrations were 0.04 and 0.004 mg/1 in April and 0 01 and <0.002 mg/1 in
August, respectively. The TNATP ratio went from 18 in April to 46 in August. Secchi depths generally
increased through the sampling period from 1.1m in April to 3.0m in October Chlorophyll a was 10 jj.g/1 in
April, increased to 12 fj.g/1 in May and July, and then dropped to 5 jj.g/1 in August as available nutrients
were depleted. The average chlorophyll a concentration was 8.9 fxg/1, in the good range (near the upper
end) for the reservoir ecological health index. Total organic carbon varied little from 3.6 mg/1 in April to
4.2 mg/1 in August. Total phosphorus and total organic carbon concentrations in the forebay were the third
highest concentrations of the 19 tributary reservoir forebays in 1993.
Sediment Quality—Chemical analyses of sediments in the forebay of Normandy Reservoir in 1993
indicated very high levels of un-ionized ammonia (720 (ig/1). Toxicity tests detected acute toxicity to
daphnids (60 percent survival) in the forebay sediment. Particle size analysis showed sediments in the
forebay were 99 percent silt and clay.
Because of the acute toxicity of the forebay sediment to daphnids and the high concentrations of
ammonia, a poor sediment quality rating was used in the 1993 Normandy Reservoir ecological health
evaluation.
Benthic Macromvertebrates—The Normandy forebay received a poor rating for its benthic
community. There were 198 organisms/m^ representing only 6 taxa; the dominant organisms were
Tubificidae, Limnodrilus sp, and Chironomus sp, which comprised 38, 35, and 24 percent of the total,
respectively The low diversity, paucity of EPT and long-lived taxa, and the abundance of tubificids all
negatively impacted the benthic community rating at the Normandy forebay.
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Fish Assemblage—Only the forebay zone was sampled on Normandy in fall 1993. Shoreline
electrofishing (15 transects) and offshore experimental gill netting (12 net-nights) yielded 1,307 individuals
with 29 species represented. Sixty-four percent of the total catch consisted of the sunfish species (rock
bass, warmouth, redbreast, green, bluegill, and longear).
The Reservoir Fish Assemblage Index (RFAI) rated the Normandy Reservoir forebay fish
community excellent, as determined by both electrofishing (RFAI=52) and gill netting (RFAI=54). The
electrofishing and gill netting RFAI's, as well as the combined scores (RFAI=53), were the highest recorded
for tributary forebays. Normandy received midrange or maximum scores in most metrics for both gear
types; the only minimum score was percent anomalies in the electrofishing sample.
Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—Two swimming beaches were tested for fecal coliform bacteria in 1993.
The geometric mean of bacteria concentrations were relatively high, 146 and 174/100 ml, but within
criterion for water contact recreation. At both sites, geometric means after rainfall were over 200/100 ml,
and both sites had three of twelve samples exceed 400/100 ml. EPA recommends that not more than
10 percent of samples exceed 400/100 ml. Both sites had large flocks of resident geese which were the
probable cause of the high fecal coliform concentrations.
Fish Tissue—Because of the small size of Normandy Reservoir, only the forebay was sampled for
fish tissue screening. Five channel catfish were collected in autumn 1992. Fillets were composited and
analyzed for selected metals, pesticides, and PCBs. Of the five metal analytes, only lead and mercury were
detected, both at low levels. The only organic analyte detected was chlordane, also at a low level
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Duck River Stream Monitoring Site
Summary of 1993 Conditions - Ecological Health
Water—The water of the Duck River is moderately hard (average hardness of 130 mg/1) and
alkaline (average total alkalinity of 118 mg/1). The median pH for the stream monitoring site was 7.7 The
river was well oxygenated with dissolved oxygen levels of 82 to 115 percent of saturation.
Of the 12 streams monitored across the Tennessee Valley, the Duck River ranked among the
highest in average concentrations of organic nitrogen (0.421 mg/1), total phosphorus (0.617 mg/1), and
dissolved orthophosphate (0.177 mg/1). The average concentrations of ammonia nitrogen (0.027 mg/1) and
nitrate+nitrite-nitrogen (0.48 mg/1) were near median for all sites. The high total phosphorus concentration
yielded a poor rating for nutrients at the site.
Seven analyses for priority pollutant metals (dissolved cadmium, lead, nickel, and zinc and total
copper and zinc) were performed bi-monthly Dissolved cadmium (4 of 6 samples) and total zinc (2 of 6
samples) were detected but neither exceeded the EPA guidelines for protection of aquatic life and human
health.
Sediment—Sediment quality rated good in 1993 with no acute toxicity observed and no metals,
PCBs. or pesticides exceeding the EPA guidelines This is an improvement over 1992 when sediment
quality rated fair
Benthic Macroinvertebrates—In 1993, benthic macroinvertebrate results rated good with a
2
Modified Benthic Index of Biotic Integrity (MBIB1) score of 47. with 105 taxa and 3,789 organisms/m
2
Conditions in 1992 rated fair (MBIBI score 34) with 61 taxa and 528 organisms/m . The benthic fauna
improved one classification since 1992. Dominant organisms in 1993 were dipteran midge larvae
(62 percent), mayflies (20 percent), and caddisflies (7 percent). Dipteran midge larvae were also the
dominant organism in 1992 (26 percent), followed by coleopteran riffle beetles (22 percent) and caddisflies
(17 percent). Excessive nutrients, streambank erosion, and substrate instability are a continuous problem at
this site.
Fish Community Assessment—The fish community rated fair with an Index of Biotic Integrity
(IBI) score of 46 and showed little improvement since it rated fair (IBI = 42) in 1992. Improvement in 1993
was seen mostly in increased fish density and absence of hybrid fish. Problems persisted in species
composition and trophic structure indicating less than optimum conditions. Diversity was low for darter,
sunfish, and intolerant species, and the proportion of tolerant fish was abnormally high. Fish most
dependent on a diverse and stable aquatic macroinvertebrate community were out-numbered by fish that
live by a more flexible feeding strategies, and the proportion of piscivorous fish was abnormally low.
Adverse conditions observed were extensive bank erosion and the predominance of unstable substrate.
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Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—Five sites on the Duck River from 1.7 miles downstream of Normandy
Dam to Shelbyville were tested for fecal coliform bacteria At the first site downstream of Normandy Dam,
the geometric mean of all fecal coliform samples was 104/100 ml. At the other four sites from 1 8 to
5.4 miles further downstream, the geometric mean ranged from 1100 to 2150/100 ml. There were several
rainstorms during the sampling period, and concentrations were much higher after rainfall. If all samples
within 24-hours of rainfall are excluded, the geometric mean of the four most downstream site range from
510 to 960/100 ml. These are among the highest concentrations found anywhere in the Tennessee Valley
during the five years of sampling under the current program. The probable cause of the high concentrations
are dairies.
Fish Tissue—A five-fish composite each of carp, channel catfish, and largemouth bass were
collected during summer 1992 and analyzed for selected metals, pesticides, and PCBs. Lead and mercury
were detected in all samples but at low concentrations. Chlordane was detected in one sample and PCBs in
two, again at only low concentrations.
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PICKWICK RESERVOIR - WILSON RESERVOIR WATERSHED
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Pickwick Reservoir
Summary of 1993 Conditions - Ecological Health
Water—During the summer of 1993 (April-September), coolest surface water temperatures in
Pickwick Reservoir were in April and the warmest in July. Surface temperatures ranged from a minimum
of 18.4°C to a maximum of 30.5°C at the forebay; from 16.2°C to 29.1°C at the transition zone; and from
22.8°C (in May-no samples in April) to 29.6°C in Bear Creek embayment. The State of Alabama's
maximum water temperature criteria for the protection of fish and aquatic life is 30.0°C.
Dissolved oxygen (DO) concentrations at the 1.5m depth ranged from a low of 6.6 mg/1 in August
to a high of 12.0 mg/1 in April at the forebay; from 6.6 mg/1 in August to 11.6 mg/1 in June at the transition
zone; and from 6.7 mg/1 in September to 10.1 mg/1 in August at the sampling location in Bear Creek
embayment. At the inflow sampling site (i.e. the tailrace of Wilson dam) a minimum DO of 3.1 mg/1 was
recorded in July. The State of Alabama's minimum dissolved oxygen criteria for the protection of fish and
aquatic life is 5.0 mg/1, measured at the 1.5 meter depth.
Temperature data depict a seasonal warming and very weak, transient thermal stratification of
Pickwick Reservoir. The maximum observed surface to bottom temperature differential (AT), in Pickwick
Reservoir in 1993 was 4.7°C at the forebay in June. However, there was a rather strong oxycline at all
three sampling locations in June and July when differences between surface and bottom DO's were about 7
to 9 mg/1 at the forebay, transition zone, and in Bear Creek embayment. In July 1993, a minimum DO of
less than 0.1 mg/1 was measured on the bottom at all three sampling locations (the forebay, transition zone,
and Bear Creek embayment) in Pickwick Reservoir. Due to the drought like conditions and low flows into
and through Pickwick Reservoir (see discussion in Section 4.0, Hydrologic Overview of 1993) sediment
oxygen demands were consuming oxygen at a rate greater than it was being replenished by inflowing water.
Flows increased to normal levels in August and September, resulting in less stratification and higher near
bottom DO levels.
DO ratings used in the overall reservoir ecological health evaluation for Pickwick Reservoir were
good at the forebay and transition zone; fair to good in Bear Creek embayment; and fair at the inflow. The
forebay, transition zone, and Bear Creek embayment would all have rated higher had it not been for the
very low near bottom oxygen concentrations which existed in July The fair rating at the inflow sampling
site on Pickwick Reservoir was a result of oxygen levels being measured approximately 2 mg/1 below the
Alabama criteria in the releases from Wilson dam in the summer of 1993 as mentioned above.
Values of pH ranged from 6.8 to 9.0 on Pickwick Reservoir in 1993. Near surface pH values
exceeding 8.5 (and DO saturation values exceeding 100 percent) were observed at all three sampling
locations. Many of these periods of high pH and high oxygen saturations were also coincident with high
chlorophyll a concentrations, indicative of periods of high photosynthetic activity. The State of Alabama's
maximum pH criteria for the protection of fish and aquatic life is 8 5.
In 1993, all three sampling locations on Pickwick Reservoir also had fairly high chlorophyll a
concentrations averaging 15 (ig/1, 12 (j.g/1, and 16.8 (a.g/1, respectively, at the forebay, transition zone, and
Bear Creek embayment. The chlorophyll a concentrations measured in Pickwick Reservoir were among the
highest measured in the Tennessee River reservoirs in 1993, indicative of eutrophic conditions.
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Consequently, the chlorophyll a ratings used in the 1993 ecological health evaluation for Pickwick
Reservoir were only fair at the forebay and transition zone, and poor in Bear Creek embayment.
Sediment—Although mercury has been found in sediment in Pickwick Reservoir at levels of
concern in past years, levels in 1993 were lower and not above sediment quality guidelines for mercury
(i.e., 1.0 mg/kg). Mercury levels in 1993 were 0.47 mg/kg at the forebay and 0.62 mg/kg at the transition
zone sampling sites. Un-ionized ammonia was detected at levels of concern (220 jj.g/1) in one of the two
forebay samples. Although no acute toxicity was detected in the main reservoir, acute toxicity to both
daphnids (30 percent survival) and rotifers (45 percent survival) was detected in the Bear Creek
embayment. Tests in 1991 and 1992 showed a potential for toxicity with MicrotoxR at the forebay. Particle
size analysis showed sediments from the forebay were about 66 percent silt and clay, 34 percent sand; from
the transition zone were 47 percent silt and clay, 53 percent sand; and from Bear Creek embayment were
99 percent silt and clay.
Sediment quality ratings used in the overall Pickwick Reservoir ecological health evaluation for
1993 were good at the forebay (presence of ammonia); excellent at the transition zone; and, fair in the Bear
Creek embayment (toxicity to the test organisms)
Benthic Macromvertebrales—The benthic communities at the forebay and inflow sites were
excellent, the transition zone was good, and the Bear Creek embayment rated fair The forebay site had 23
taxa and 533 organisms/m2 with Coelotanvpus sp (26 percent), Corbicula fluminea (20 percent), and
Hydrobiidae (15 percent) as the dominant taxa. The transition zone had a slightly more diverse fauna than
2
the forebay, with 25 taxa and 745 organisms/m . Corbicula fluminea (23 percent) and Hexagenia sp
(21 percent) were the most abundant taxa. The inflow had the greatest diversity and of all sites sampled,
with 42 taxa and 699 organisms/m2. The benthic community there was dominated by Corbicula fluminea
(65 percent).
Bear Creek embayment, a major component of Pickwick Reservoir, was also sampled and received
a fair rating. It had a total of 1,188 organisms/m2 and 15 taxa. Tubificidae (33 percent), Einfeldia
(25 percent) and Coelotanypus tricolor (21 percent) were the dominant taxa. Although this site had a good
diversity of benthic organisms and an evenness of dominant taxa, the abundance of chironomids and the
paucity of EPT taxa contributed to this site only receiving a fair rating.
Aquatic Macrophytes—There were an estimated 105 acres of submersed plants on Pickwick
Reservoir in 1993, primarily in the upstream portion of Yellow Creek embayment. Historically, most of the
aquatic vegetation on Pickwick Reservoir has been in the Yellow Creek embayment, and in 1993 naiads
and muskgrass were the most abundant macrophytes.
Fish Assemblage—Fish collections at near shore areas (45 clectrofishing transects) and offshore
bottom areas (30 net-nights) from the three zones of Pickwick Reservoir resulted in the collection of 2,526
fish including 42 species. Three non-game species, including skipjack herring, gizzard shad, and brook
silvcrsidc, comprised 50 percent of all fish collected Other dominant species groups were the sunfishes
(green, bluegill, longear, and redear), catfishes (blue, channel, and flathead), and black basses (smallmouth,
spotted, and largemouth), which made up 12, 7, and 6 percent of the total sample, respectively Fish
22
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abundance was greatest in the forebay zone (1,563) followed by the transition (659), and inflow zones
(304). Total catch was significantly higher in the forebay than the other two zones with both gear types
(even considering reduced netting effort in the inflow).
The Reservoir Fish Assemblage Index (RFAI) rated the littoral fish community (based on results of
electrofishing samples) good in all three zones of the reservoir (forebay RFAI=46, transition RFAI=42, and
inflow RFAI-46). The Pickwick forebay score of 46 was, along with Wilson forebay, the highest recorded
in run-of-the-river reservoirs in 1993. The slightly lower transition score was influenced by lesser numbers
of piscivorous and sunfish species. The gill netting RFAI rated the transition (RFAI=46) and forebay
(RFAI=42) good. Gill netting RFAI values were not calculated for inflow zones of run-of-the-river
reservoirs. Combined electrofishing and gill netting RFAI scores for the forebay (RFAI =44), transition
(RFAI=44), and the electrofishing RFAI for the inflow (RFAI=46) rated all areas as good.
Fish samples taken in the shoreline areas (15 electrofishing transects) and offshore/deep areas (12
net-nights) in Bear Creek embayment produced a total of 975 individuals represented by 36 species. By far
the two most dominant species were gizzard shad (35 percent) and skipjack herring (22 percent). No other
species were captured in significant numbers Number of individuals captured was similar with both gear
types.
Both electrofishing (RFAI=42) and gill netting (RFAI=46) RFAI's rated the Bear Creek
embayment good, ranking it the highest of the four embayment study sites Both gear types received the
highest score for five of the twelve metrics.
Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—Four swimming beaches and six informal swimming areas were tested
for fecal coliform bacteria in 1993. Bacteria concentrations at all ten sites were very low (geometric mean
<20/100 ml). There were no significant rainfall events during the survey. This may have contributed to the
very low concentrations at some sites. Monthly sampling at the three Vital Signs locations (forebay,
transition zone, and Bear Creek Embayment) produced equally low fecal coliform concentrations.
Fish Tissue—One composite sample of five channel catfish was collected at the forebay, transition
zone, and inflow in autumn 1992. Concentrations of all metals were low. Mercury was detected in most
samples but at relatively low concentrations (maximum of 0.24 jig/g). Pesticides and PCBs were generally
low. The exception was DDTr, which was relatively high at the inflow (2.4 |ig/g) yet not detected at the
other two locations. This is not thought to represent a problem because concentrations of this magnitude
have not been observed in previous years of screening. It is possible that one of the catfish in the composite
was from Wheeler Reservoir where there is a problem with DDT contamination in one area resulting in
high concentrations in fish Relatively high concentrations of chlordanc in 1990 were not found in 1991 or
1992. PCBs were detected in all samples (range 0.2 to 0.7 (ig/g) with concentrations tending to be higher at
the inflow. Samples were recollected at the inflow site in autumn 1993 to ensure that a possible problem
with DDTr, chlordane, or PCBs is not overlooked; results were not available at the time this report was
prepared.
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24
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Wilson Reservoir
Summary of 1993 Conditions - Ecological Health
Water—During the summer of 1993 (April-September), surface water temperatures ranged from
13 7°C in April to 31.6°C in July at the forebay sampling location. Temperatures above 30.0°C exceed
State of Alabama water quality criteria for fish and aquatic life. Values for DO at the 1.5m depth ranged
from a high of 13.8 mg/1 in May (during a large algal bloom) to a low of 5.7 mg/1 in September at the
forebay. At the Wheeler dam tailrace a minimum DO of 4.3 mg/1 was recorded in July. The State of
Alabama's minimum dissolved oxygen criteria for the protection of fish and aquatic life is 5.0 mg/1,
measured at the 1.5 meter depth.
Temperature and DO data show seasonal warming and both thermal and oxygen stratification in
the forebay from May through August. The greatest degree of thermal stratification was observed in July,
as might be expected, during the period of high temperatures and low flows (see discussion in Section 3.0,
Hydrologic Overview of 1993). In July, temperatures at the forebay ranged from 31.6°C (surface) to
21.5°C (bottom), a differential of 10.1 °C.
Periods of strong DO stratification, with surface to bottom DO differentials ranging from about 7
to 12 mg/1, were also observed during these four months, May through August. For example, in June,
surface DO concentrations of about 12 mg/I (during a large algal bloom) were contrasted with near bottom
DO concentrations of about 0 mg/1. The depth of Wilson Reservoir (approximately 100 feet at the dam)
and the unseasonably low flows during the summer of 1993 combined to have a pronounced effect on
hypolimnetic DO in Wilson forebay, Bottom DO concentrations were at or near 0 mg/l for approximately
three months (June, July, and August), and the volume of hypolimnetic anoxia was greater in the summer
of 1993 than has been observed in the prior three years of Vital Signs monitoring (1992 to 1990). For the
summer, DO concentrations in Wilson forebay averaged only 5.9 mg/1, lower than at any other Vital Signs
monitoring location on run-of-the-river reservoirs.
Consequently, the forebay DO rating used in the overall ecological health rating of Wilson for
1993 was very poor. A good rating for DO was assigned to the Wilson reservoir inflow sampling site (i.e.,
Wheeler dam tailrace) because oxygen levels fell only slightly below 5 mg/1 in releases from Wheeler dam
during the summer of 1993 (l e. DO's less than State of Alabama's 5 mg/1 criteria, measured at the 1.5
meter depth).
Values of pH ranged from 6.7 to 9.1. In May and June near-surface values of pH were measured
greater than 9 0 These high pH values coincided with periods of high photosynthetic activity, high
temperatures, high dissolved oxygen measurements (percent oxygen saturation values exceeding 150%),
and high chlorophyll a concentrations. The State of Alabama's maximum pH criteria for the protection of
fish and aquatic life is 8.5
Summer chlorophyll a concentrations in Wilson forebay averaged about 10.2 jag/1 in 1993, slightly
higher than preferred, but much better than in 1992 when a massive algal bloom (chlorophyll a
concentrations of 146 jag/1) occurred in May on Wilson reservoir. A forebay chlorophyll a rating of fair
was used in the ecological health evaluation of Wilson Reservoir in 1993.
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Historically, the water in the forebay of Wilson is quite clear relative to the other Tennessee River
reservoirs. In the summer of 1993, Secchi depths averaged over 1.7 meters and suspended solids (TSS)
averaged only about 3.2 mg/1, among the highest Secchi's and lowest TSS's measured on the run-of-the-
river reservoirs.
Sediment—Chemical analyses of sediment did not reveal any metal or organic analyte to be a
concern. Toxicity tests detected no acute toxicity to either species tested; however, reduced survival of
rotifers (65 and 85 percent survival) was seen in samples from the forebay. Toxicity to rotifers was
detected in 1991. Particle size analysis showed sediments from the forebay were about 99 percent silt and
clay.
The forebay sediment quality rating used in the overall Wilson Reservoir ecological health
evaluation for 1993 was very good, instead of excellent, due to the slightly reduced survival of rotifers.
Benthic Macromvertebrates—Wilson forebay and inflow sites showed improvements in their
benthic communities. The forebay improved from poor to fair, and the inflow from good to excellent. The
2
forebay had 803 organisms/m representing 22 taxa with Chironomus sp (42 percent) as the dominant
2
organism. The inflow site had 683 organisms/m representing 48 taxa with Corbicula sp (41 percent) as
the dominant organism.
The Wilson forebay scored as high as possible on three metrics, taxa richness, percentage of the
community comprised of tubificids, and the evenness of dominant organisms. The two metrics that brought
down the overall benthic score were the high numbers of chironomids present and the low number of EPT
taxa present. These factors resulted in a fair rating for the forebay site. The inflow site received a perfect
score for every metric and received an excellent rating. This epitomizes a healthy benthic community: high
diversity, the presence of a good EPT community, an abundance of long-lived organisms, low numbers of
tubificids and chironomids, and an evenness of dominant organisms
Agnatic Macrophytes—There were 54 acres of aquatic plants on Wilson Reservoir in 1993.
Muskgrass was the dominant species and colonized shallow water sloughs. Eurasian watermilfoil
historically occurred as localized populations on Wilson Reservoir, but has not been observed on Wilson in
several years
Fish Assemblage—Shoreline electrofishing (30 transects) and offshore gill netting (19 net-nights)
at the forebay and inflow of Wilson Reservoir produced 3,567 individuals of 38 species, and showed fish
were most abundant in the inflow (69 percent of the total fish collected). Species representing the largest
portion of the Wilson fish assemblage included emerald shiners (25 percent), brook silversides (22 percent),
gizzard shad (19 percent), and bluegill (11 percent). Most of the inflow electrofishing catch (66 percent)
consisted of emerald shiners and gizzard shad. There were also moderate numbers (CPUE= 234 per
transect) of young-of-year (YOY) threadfin shad in the inflow area.
The 12 electrofishing RFAI metrics described the littoral fish community of both the inflow
(RFA1=42) and the forebay (RFAI=46) zones as good. The Wilson and Pickwick forebay ratings of 46
were the highest recorded in run-of-the-river reservoirs in 1993. The 1993 forebay (RFAI=46) rating also
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represented an increase over the 1992 RFAI score of 38. The forebay scores were the same or higher for all
metrics with exception of the average number of individuals (i.e., average catch per transect). The gill
netting RFAI rated the forebay (38) fair. Gill netting RFAI values were not calculated for inflow zones of
run-of-the-river reservoirs due to low numbers of replicate samples. Combined electrofishing and gill
netting RFAI scores rated the forebay (RFAI=42) and the electrofishing RFAI for the inflow (RFAI=42)
good.
Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—The boat ramps at Fleet Hollow and Lock Six were tested for fecal
coliform bacteria in 1993. Bacteria concentrations were very low (geometric mean <20/100 ml). The
monthly Vital Signs samples collected in the forebay were all less than 10/100 ml.
Fish Tissue—Composited channel catfish samples were collected from the forebay and inflow
areas in autumn 1992. All analytes were low or not detected. PCB concentrations have been relatively high
in occasional samples during past years Interestingly, 1992 samples from both locations were below the
detection limit.
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Bear Creek Reservoir
Summary of 1993 Conditions - Ecological Health
Water—The average flow in 1993 was about 89 percent of normal Even with the relatively short
average residence time, 14.4 days, the maximum temperature difference in the forebay water column was
14.6°C in July. The maximum surface temperature was 31 3°C in July. The Alabama maximum water
temperature criterion for fish and wildlife is 32.2°C (90 F). Depleted DO conditions began at the bottom in
May and by June 21 the area of DO <2.0 mg/1 extended to within four meters of the surface, resulting in a
poor DO rating in the reservoir's ecological health index. The cooling surface temperatures in September
allowed surface mixing with the metalimnion, extending the depth with DO >2.0 mg/1 to seven meters.
Conductivities in April were about 50 ^mhos/cm. Conductivities in the DO depleted zone rose
throughout the summer reaching 182 fimhos/cm in September. The maximum pH was about 8.5 at the
surface in July. The minimum pH was about 6 1 in the upper portion of the depleted DO zone in August
and September.
The total nitrogen concentration was 0.79 mg/1 in April, about 60 percent as nitrates. By August,
nitrates had disappeared, reducing the total nitrogen concentration to 0.37 mg/1 Total phosphorus and
dissolved ortho phosphorus concentrations were 0.02 and 0.002 mg/1 in April, and 0.01 and <0.002 in
August, respectively. The TN/TP ratio was between 37 and 40 in both surveys. Secchi depths were the
lowest of the 19 tributary reservoir forebays, ranging from 0 75 to 1.75 meters. Chlorophyll a
concentrations were the highest of the 33 tributary stations, ranging from 8 to 17 ng/1. The average
chlorophyll a concentration of 12 3 [o.g/1 gave Bear Creek a fair rating for chlorophyll in the reservoir's
ecological health index. Total organic carbon concentrations were 2.5 and 2 8 mg/1 in April and August,
respectively.
Sediment Quality—Chemical analyses of sediments in the forebay of Bear Creek Reservoir in
1993 indicated elevated levels of un-ionized ammonia (280 |ig/l). Toxicity tests detected acute toxicity to
daphnids (0 percent survival) and rotifers (65 percent survival) in the forebay sediment. Particle size
analysis showed sediments in the forebay were 94 percent silt and clay.
Because of the acute toxicity of the forebay sediment to daphnids and rotifers and the presence of
ammonia, a very poor sediment quality rating was used in the overall 1993 Bear Creek Reservoir ecological
health evaluation.
Benthic Macromvertebrates—Bear Creek forebay, the only site sampled on the reservoir, had 18
2
taxa and 216 organisms/m . Prodadius sp accounted for 37 percent of the total Bear Creek forebay
supported an excellent bcnthic community in 1993, with 5 of the 6 metrics receiving a good score. The
proportion of the sample comprised by chironomids was the only metric to receive a poor score.
Fish Assemblage—Only the forebay zone was sampled on Bear Creek Reservoir in fall 1993.
Electrofishing samples (15 transects) in shoreline areas and experimental gill netting samples (12 net-
nights) offshore collected 1,632 individuals with 28 species represented. Blucgill was the most abundant
taxon in Bear Creek Reservoir (28 percent of total fish sampled) Green sunfish (14 percent), gizzard shad
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(7 percent), spotted bass (7 percent), and longear sunfish (6 percent) followed in order of density. Species
diversity was much higher in electrofishing samples (24 species) than in gill netting efforts (14 species).
The Reservoir Fish Assemblage Index (RFAI) rated the littoral fish community (based on results of
electrofishing samples) excellent (RFAI=52) and received maximum scores in all metrics except percent
tolerant species, average number of individuals, and percent anomalies. Fifty-two was the highest RFAI
recorded in all TVA tributary reservoir forebays (Normandy Reservoir forebay also scored 52). The gill
netting RFAI of 40 was rated fair. The combined electrofishing and gill netting RFAI of 46 rated Bear
Creek forebay good.
Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—The swimming beaches at Piney Point and Horseshoe Bend were tested
for fecal coliform bacteria in 1993. Bacteria concentrations were very low (geometric mean <20/100 ml)
except for one sample at Horseshoe Bend (4800/100 ml).
Fish Tissue—A five fish composite of channel catfish was collected from the forebay during
autumn 1992. There were no pesticides or PCBs detected in the sample. Of the five metals examined, only
mercury was found above the detection limit. The concentration (0.45 (ig/g) was relatively high, although
far below the concentration of 1.0 fig/g used by the U.S. Food and Drug Administration to remove products
from commerce. Another sample of channel catfish was collected from the same area in autumn 1993 to
further evaluate this result.
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Little Bear Creek Reservoir
Summary of 1993 Conditions - Ecological Health
Water—The average flow through the reservoir in 1993 was about 89 percent of normal, with an
average residence time of 254 days. The reservoir was thermally stratified throughout the sampling period
with a maximum temperature difference in the water column of 20.5°C in July. The maximum surface
temperature of 31.1 °C in July was less than the Alabama water quality criterion for fish and wildlife of
32.2°C (90 F). The area of DO depletion (DO < 2.0 mg/1) began at the bottom in June, extended to within
8 meters of the surface in July and August, and still comprised over one-half the water column in October.
This resulted in a poor DO rating in the reservoir ecological health index. During June, very high DO
concentrations and corresponding high pH values occurred in the metalimnion. DO was 16.2 mg/1 and pH
was 9 4 at the six meter depth; a DO saturation of 172 percent. This was below the area at which the
composited surface sample was collected, thus the chlorophyll concentration in June was probably much
higher than the measured 5 (ig/1.
Surface pH varied from 8.0 to 8.9 from April to August. The minimum pH was 6 7 near the
bottom in September. Conductivities throughout the water column were slightly over 100 ^mhos/cm until
DO was depleted at the bottom. Then bottom conductivities rose continually to a maximum of
167 ^mhos/cm in October.
Organic nitrogen concentrations were constant, 0.28 mg/1 in April and 0.29 mg/1 in August, while
nitrates dropped from 0.2 mg/1 in April to <0.01 mg/1 in August. Total and dissolved ortho phosphorus
concentrations were 0.02 and 0.002 mg/1 in April and 0.008 and <0 002 mg/1 in August. Total organic
carbon concentrations were 2.3 mg/1 in April and 2.9 mg/1 in August The water was relatively clear, with
Secchi depths ranging from 2.0 meters in April to 4.0 meters in August. Productivity was relatively
low—the chlorophyll concentration averaged 3.8 (ig/1 with a maximum of 7 p.g/l in August. These
chlorophyll concentrations are in the range considered good in the reservoir ecological health index.
Sediment Quality—Chemical analyses of sediments in the forebay of Little Bear Creek Reservoir
in 1993 did not reveal any metal or organic analyte to be a concern. Toxicity tests detected acute toxicity to
daphnids (45 percent survival) in the forebay sediment. This resulted in a fair rating for sediments in the
ecological health index. Particle size analysis showed sediments in the forebay were 94 percent silt and
clay.
Benthic Macroirrvertebrates—The Little Bear Creek forebay site had a fair benthic community,
2
with high densities and low diversity. There were 3,898 organisms/m representing only 11 taxa, primarily
Tubificidae (96 percent of the total). The abundance of Tubificidae, essentially a tolerant family, had the
largest negative impact on the benthic community The metrics of number of EPT taxa, number of long-
lived taxa, and diversity all received fair scores The only metric to receive a good score was the low
proportion of the sample comprised of chironomids.
Fish Assemblage—Only the forebay was sampled on Little Bear Creek Reservoir in fall 1993.
Shoreline electrofishing (15 transects) and offshore experimental gill netting (10 net-nights) yielded 2,946
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individuals represented by 27 species. Thirty-eight percent of the total catch consisted of bluntnose
minnows, followed by bluegill (21 percent), largemouth bass (6 percent), and green sunfish (5 percent)
The primary forage base in Little Bear Creek Reservoir was comprised mainly of sunfish and minnows, as
shad were collected in very low numbers in both electrofishing and gill netting samples.
Fish assemblage rated good for both electrofishing (RFAI=46) and gill netting (RFAI=50) in the
forebay. Scores for the electrofishing sample were midrange or maximum for all metrics except number of
piscivore species and percent omnivores. Scores in the gill netting samples were midrange or maximum for
all metrics. The overall RFAI (combining electrofishing and gill netting results) rated Little Bear Creek
forebay as good.
Summary of 1993 Conditions - Use Suitability
Fecal Cohform Bacteria—The swimming beaches at Eliott Branch and Williams Hollow were
tested for fecal coliform bacteria in 1993. Bacteria concentrations were vers' low (geometric mean
<20/100 ml).
Fish Tissue—A five-fish composite of channel catfish was collected from the forebay in autumn
1992. There were no pesticides or PCBs detected in the sample. Mercury was the only metal analyte found;
arsenic, cadmium, lead, and selenium were not detected. The mercury concentration (0.56 |ig/g) was high
enough to warrant further examination in autumn 1993 but not high enough to warrant a detailed study.
The 1993 results were not available at the time this report was prepared.
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Cedar Creek Reservoir
Summary of 1993 Conditions - Ecological Health
Water—The average flow was about 90 percent of normal The average residence time was about
186 days, and thermal stratification was moderate to strong. The maximum temperature difference in the
water column was 17.9°C in July. The maximum temperature was 30.9°C in July, less than the Alabama
water quality criterion for fish and wildlife of 32.2°C (90 F). DO depletion (DO < 2.0 mg/l) began at the
bottom in May, extended to within 7 meters of the surface in August, and remained depleted at the bottom
in October. This resulted in a poor rating for DO in the reservoir ecological health index. Conductivities in
Cedar Creek were the third highest of the 19 tributary reservoirs, averaging about 240 |imhos/cm in the
water column in April, and increasing in the anoxic zone throughout the summer to a maximum of 295
|imhos/cm at the bottom in October Surface pH was over 8.0 from April through September, with a
maximum of 8 6 in May. Cedar Creek water is slightly basic, the minimum bottom pH was 7.1 in
September.
Both organic and nitrate nitrogen concentrations decreased sharply from April to August. Organic
nitrogen concentrations were 0.41 and 0.11 mg/l, while nitrate concentrations were 0.17 and <0.01 mg/l,
respectively. Total and dissolved ortho phosphorus concentrations were 0 02 and 0.004 mg/l in April, and
0.004 and <0.002 mg/l in August. Total organic carbon concentrations were 2.9 and 2.7 mg/l in April and
August, respectively. Water clarity was low to moderate, Secchi depths varied from 1.0 meter in April to
2.75 meters in June Chlorophyll a concentrations were low, averaging 2.8 jag/1 with a maximum of 5 fig/1
in May. These low chlorophyll concentrations gave Cedar Creek Reservoir a fair chlorophyll rating in the
reservoir ecological health index.
Sediment Quality—Chemical analyses of sediments in the forebay of Little Bear Creek Reservoir
in 1993 did not reveal any metal or organic analyte to be a concern. Toxicity tests detected acute toxicity to
daphnids (45 percent survival) in the forebay sediment. Particle size analysis showed sediments in the
forebay were 94 percent silt and clay.
Because of the acute toxicity of the forebay sediment to daphnids, a fair sediment quality rating
was used in the overall 1993 ecological health evaluation.
Benthic Macroinvertebrates—The Cedar Creek forebay supported a fair benthic community with
2
387 organisms/m representing 10 species. Chironomus sp and Tubificidae were the dominant taxa,
comprising 42 and 40 percent of the total, respectively. All 6 metrics received a fair score
Fish Assemblage—Only the forebay zone was sampled on Cedar Creek Reservoir in fall 1993.
Shoreline electrofishing (15 transects) and offshore experimental gill netting (12 net-nights) yielded 662
individuals represented by 18 species (second lowest diversity' in all TVA reservoirs). Thirty-eight percent
of the total catch consisted of brook silversides, followed by gizzard shad (20 percent), spotted bass
(13 percent), and spotted suckers (11 percent)
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The Reservoir Fish Assemblage Index (RFAI) rated the forebay of Cedar Creek Reservoir fair
(RFAI=32) as determined by electrofishing samples and good (RFAI=46) as determined by gill netting. The
low electrofishing rating could be attributed to low diversity, and low catch. Combined electrofishing and
gill netting ratings (RFAI=38) determined the reservoir fish community to be fair.
Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—The swimming beach at Slickrock Ford was tested for fecal coliform
bacteria in 1993. Bacteria concentrations were very low (geometric mean <20/100 ml).
Fish Tissue—Five channel catfish were collected from the Cedar Creek forebay in autumn 1992.
Composited fillets were analyzed for pesticides, PCBs, and selected metals. All pesticides and PCBs were
below detection limits. Of the five metal analytes, only mercury was detected - at a relatively low
concentration of 0.21 (ig/g.
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Bear Creek Stream Monitoring Site
Summary of 1993 conditions - Ecological Health
Water— The water of Bear Creek is soft (average hardness of 50 mg/1) and moderately alkaline
(average total alkalinity of 50 mg/1). The median pH for the stream monitoring site was 7.6 . The river is
well oxygenated with dissolved oxygen levels ranging from 80 to 94 percent of saturation.
Of the 12 streams monitored across the Tennessee Valley, Bear Creek ranked among the lowest in
average concentrations of nitrate+nitrite-nitrogen (0.24 mg/1) and dissolved orthophosphate (0.005 mg/1). It
was among the highest stations with average ammonia nitrogen and organic nitrogen concentrations of
0.044 mg/1 and 0.332 mg/1. The average total phosphorus concentration of 0.065 mg/1 was near the median
for all stations. The fair total phosphorus and acceptable nitrate+nitrite-nitrogen concentrations yielded a
fair rating for nutrients at the site.
Seven analyses for priority pollutant metals (dissolved cadmium, lead, nickel, silver, and zinc and
total and dissolved copper and zinc) were performed bi-monthly. Dissolved cadmium (6 of 6 samples),
dissolved nickel (2 of 6 samples), and dissolved zinc (1 of 6 samples) were detected, but at levels within the
EPA guideline for protection of human health and aquatic life. Dissolved lead in one of six samples
exceeded the EPA guideline for chronic toxicity to aquatic life.
Sediment—Sediment quality rated good in 1993 with no acute toxicity observed and no metals,
PCBs, or pesticides exceeding the EPA guidelines. This is an improvement over 1992 when sediment
quality rated fair.
Benthic Macroinvertebrates—In 1993, benthic macroinvertebrate results rated fair with a
2
Modified Benthic Index of Biotic Integrity (MBIBI) score of 40, with 91 taxa and 1,697 organisms/m .
2
Conditions in 1992 also rated fair (MBIBI score 38) with 74 taxa and 2,044 organisms/m The number of
taxa was greater in 1993 but densities were lower. The benthic fauna in 1993 was composed mostly of
dipteran midge larvae (31 percent), the Asian clam Corbicula (22 percent), and river snails (21 percent).
Dipteran midge larvae were also dominant in 1992 (52 percent), followed by Asian clams (17 percent) and
nutrient-tolerant oligochaeta worms (12 percent). Streambank erosion and unstable substrates are a
continuing problem affecting benthic organisms at this site.
Fish Community Assessment—The fish community rated fair with an Index of Biotic Integrity
(IB1) score of 40), deteriorating considerably from the good (IBI = 48) rating in 1992. Fish sampled in
1993 included fewer native species and fewer intolerant species. A decrease was also seen in the proportion
of specialized insectivores, fish that depend most on a diverse and stable macroinvertebrate community.
Fish density changed most drastically, declining by approximately 50 percent since 1992. Adverse
conditions observed at this station include extensive bank erosion and a predominance of shifting gravel
substrate.
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Summary of 1993 conditions - Use Suitability
There were no bacteriological samples or fish tissue samples collected from the Bear Creek stream
site in 1993.
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WHEELER RESERVOIR - ELK RIVER WATERSHED
37
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Wheeler Reservoir
Summary of 1993 Conditions - Ecological Health
Water—Wheeler Reservoir was generally well mixed and lacked persistent thermal stratification in
1993. During the April-September monitoring period, coolest surface water temperatures in Wheeler
Reservoir were in April and the warmest in July. Surface temperatures ranged from a minimum of 17.3°C
to a maximum of 31.9°C at the forebay; from 15.4°C to 29.6°C at the transition zone; and from 18.7°C to
31,2°C in the Elk River embayment. The 31,9°C temperature in the forebay of Wheeler Reservoir was the
warmest Tennessee River temperature measured as part of the Vital Signs monitoring program (1990-
1993), and is evidence of the effect the very warm meteorological conditions had on surface water
temperatures in July of 1993. (Sec discussion in Section 4.0, Hydrologic Overview of 1993). Temperatures
above 30.0°C exceed the State of Alabama's water quality criteria for fish and aquatic life.
Dissolved oxygen (DO) concentrations at the 1.5m depth ranged from a low of 6.6 mg/1 in
September to a high of 11.6 mg/1 in April at the forebay; from 6.2 mg/1 in August to 9.4 mg/1 in April at
the transition zone, and from 6.1 mg/1 in September to 14.1 mg/1 in April at the sampling location in the Elk
River embayment. At the inflow sampling station site (i.e. the tailrace of Guntcrsville dam) a minimum DO
of 5.4 mg/1 was recorded in July. The State of Alabama's minimum dissolved oxygen criteria for the
protection of fish and aquatic life is 5.0 mg/1, measured at the 1.5 meter depth
Temperature data give evidence of the seasonal warming and a weak thermal stratification in the
downstream portion of Wheeler Reservoir (i.e at the forebay and Elk River embayment). The maximum
surface to bottom temperature differential (AT) occurred in June and was 5.8°C at the forebay and 7 0°C in
the Elk River embayment. The transition zone was well mixed throughout the summer with AT's almost
never exceeding 1.0°C.
As was the case for several other Tennessee River reservoirs, during the drought like conditions of
the summer of 1993, a strong oxyclme developed in June, July, and August in the downstream portions of
Wheeler Reservoir. At the forebay, surface to bottom DO differentials (DO) were 9.7, 9.5, and 7.1 mg/1,
respectively, in June, July, and August. In the Elk River embayment DO's of 11.0, 10.4, and 11.4 mg/1
were measured in June, July, and August, respectively. As strcamflows decreased and water temperatures
increased, naturally occurring decomposition processes at the bottom of the reservoir used available oxygen
at a rate faster than it was replenished by inflows DO's at or near 0 mg/1 occurred at the bottom in the
forebay in July; and in the Elk River embayment in June, July, and August. However, in contrast, the
transition zone was well mixed and lacked any DO stratification (DO differentials never exceeded 1 mg/1
and minimum DO's were never less than 6 mg/1) In addition, DO's were never observed to fall below
5 mg/I at the inflow sampling site (i.e. the tailrace of Guntersville dam).
Based on the above information, the DO component of the overall reservoir ecological health
evaluation for Wheeler Reservoir rated poor at the forebay and Elk River embayment; and excellent at the
transition zone and inflow The forebay and Elk River embayment rated poor because of the near bottom
anoxia and the duration and volume of water with oxygen concentrations less than 2 mg/1.
Values of pH ranged from 6 7 to 9.1 in Wheeler Reservoir during the summer of 1993. Near
surface values of pH equal to or greater than 8.5 were observed in April, June, July, and August at the
forebay and in the Elk River embayment; but no pH's were ever less than 7.2 nor greater than 7.8 at the
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transition zone. Coincident with these pH's greater than 8.5 (particularly in the Elk River embayment) were
oxygen saturation values ranging from 120% to 175% and high chlorophyll a concentrations, evidence of
very high photosynthetic activity.
Ammonia nitrogen concentrations measured in Wheeler Reservoir, at both the forebay and the
transition zone, were relatively high. As has been the case in previous years (1990-1992), ammonia
nitrogen concentrations measured in 1993 were higher than at any other Vital Signs Monitoring location on
the Tennessee River and averaged approximately 0.07 mg/1 at the forebay and 0.11 mg/1 at the transition
zone. Given the volume of flow of the Tennessee River through Wheeler Reservoir and the lack extended
periods of anoxia, the high ammonia concentrations could be indicative of large point and non-point waste
discharge(s) to Wheeler Reservoir.
Historically (1990-1992), the forebay of Wheeler Reservoir has the highest total organic carbon
(TOC) and organic nitrogen concentrations of any Vital Signs sampling site on the Tennessee River. In
1993, TOC averaged 2.6 mg/1 (one of the highest TOC concentrations) and organic nitrogen averaged
0.32 mg/1 (highest organic nitrogen concentration among the Tennessee River sampling sites) at the
forebay. These data and other water quality characteristics (total phosphorus, total nitrogen, and
chlorophyll a,) show substantial increases in concentration between the transition zone sampling site at
Tennessee River Mile (TRM) 295 .9 and the forebay sampling site at TRM 277.0. These data suggest a
dramatic increase in primary productivity between the two sampling sites, likely stimulated by the input of
large amounts of nutrients from the Elk River which joins Wheeler Reservoir about seven miles upstream
of the forebay at TRM 284.3. The Elk River has a median total phosphorus and total nitrogen
concentration of about 0.18 mg/1 and 1.10 mg/1, respectively, and an annual mean daily flow of about 3050
cfs (For additional information see discussion below on the Elk River embayment.)
The dramatic increase in primary productivity in Wheeler Reservoir between the transition zone
and the forebay is reflected in the chlorophyll a results. During the summer of 1993, chlorophyll a
concentrations measured at the forebay were as high as 24 (J.g/1 in April and August, and averaged about
13.5 jig/1. This is over a 300% increase in chlorophyll a concentrations from those measured at the
transition zone, where chlorophyll a concentrations averaged only about 4 fig/1 during the summer of 1993.
Water quality in the Elk River embayment was unique in several aspects, largely reflecting the
natural characteristics of the Elk River. During the summer of 1993, concentrations of several water
quality parameters were higher in the Elk River embayment than at any other embayment or run-of-the-
river sampling site. For example, total nitrogen and ammonia nitrogen averaged 0.72 mg/1 and 0.11 mg/1,
respectively. Total phosphorus and dissolved ortho phosphorus averaged 0.175 mg/1 and 0.067 mg/1,
respectively. Consequently, as might be expected, chlorophyll a concentrations were very high, averaging
23 (j.g/1 and with concentrations as high as 39 pg/l measured during massive algal blooms. These
chlorophyll a concentrations measured in the Elk River embayment were higher than at any of the other
Vital Signs monitoring locations during 1993.
The chlorophyll a ratings used in the 1993 ecological health evaluation for Wheeler Reservoir were
fair at the forebay (average exceeding 10 |ag/l), good at the transition zone, and poor in the Elk River
embayment (average exceeding 15 (ig/1 and large algal blooms).
Finally, true color values in the forebay of Wheeler Reservoir are among the highest measured on
the Tennessee River and show a relatively large increase between the transition zone and the forebay. The
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1990-1992 average for true color was 15.4 and 11.8 PCU's at the forebav and transition zone, respectively.
During the summer of 1993, true color values averaged 12.5 PCU's at the forebay (the highest among the
Tennessee River sampling sites in 1993) and 7.0 PCU's at the transition zone (one of the lowest of the
Tennessee River sampling sites in 1993). These summer color values at the forebay are even higher than
those measured throughout the year in the Elk River, which averaged about 12 PCU's, from 1986-1991.
These data suggest that even though some color is added to the Tennessee River by inflows from the Elk
River, there are other additional sources of color to Wheeler Reservoir between the transition zone and the
forebay.
Sediment Quality—Chemical analyses of sediment in Wheeler Reservoir in 1993 indicated elevated
levels of un-ionized ammonia (340 ng/1) from the Elk River embayment. Toxicity tests did not reveal acute
toxicity to daphnids or rotifers from the three sites tested. Particle size analysis showed sediments from the
forebay were 98 percent silt and clay, from the transition zone were 25 percent silt and clay, 75 percent
sand; and from the Elk River embayment were 73 percent silt and clay, 27 percent sand.
Sediment quality ratings used in the overall Wheeler Reservoir ecological health evaluation for
1993 were excellent at the forebay and transition zone; and slightly lower, i e. good, in the Elk River
embavment due to the presence of ammonia
Benthic Macromvertebrates—The benthos rated fair at the forebay in 1993, same as in 1992. The
transition zone improved from fair in 1992 to good in 1993, and the inflow improved from good in 1992 to
excellent in 1993. A major are of Wheeler Reservoir, the Elk River embayment, was sampled for the first
7
time in 1993 and received a poor rating. The forebay location had 14 taxa and 633 organisms/m ,
dominated by the chironomid Coelotanvpus (71 percent). The transition zone had 32 taxa and 870
"2
organisms/m , with Hexagenia limbata as the dominant taxon comprising 38 percent of the total. The
2
inflow site had 30 taxa present and 651 organisms/m with Corbicula fluminea as the dominant organism
2
present (61 percent) The Elk River embayment had 25 taxa and 1,488 organisms/m with Tubificidae
(37 percent) and Coelotanvpus sp (16 percent) as the two dominant taxa.
Wheeler forebay received a fair rating; this is partially due to the high numbers of chironomids and
low EPT taxa present at the site. Interestingly, tubificids made up only a small portion of the sample, and
this boosted the rating slightly. The other metrics, taxa richness and abundance of long-lived species, were
mediocre. At the transition site, a good rating was attained because of good diversity, EPT taxa richness,
and low numbers of chironomids and tubificids. The only metric that brought the rating down was the
evenness of dominant organisms; in this case one organism comprised an inordinate amount of the total
organisms present The inflow site on Wheeler received a perfect score due to its taxa richness, presence of
a good EPT community, presence of several long-lived taxa, evenness of dominant organisms, and low
numbers of tubificids and chironomids. Elk River embayment did not fare as well as the rest of the sites on
Wheeler, primarily because it had large numbers of chironomids and tubificids, and very few EPT taxa and
long-lived organisms. A perfect score on the taxa richness metric kept this site from receiving a very poor
rating.
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AquaticMacrophytes—Aquatic plants increased from 4,412 acres in 1992 to 6,597 acres in 1993.
Wheeler Reservoir had the second largest amount of aquatic vegetation within the TVA system. Dominant
submersed species were Eurasian watermilfoil and spinyleaf naiad. These were most abundant in shallow
overbank habitats from TRM 296 upstream to TRM 309. Wheeler Reservoir also had large populations
(1,431 acres) of American lotus concentrated in Flint Creek embayment, overbank sloughs upstream of
Flint Creek, and in Swan Creek embayment.
Fish Assemblage—Fish data collected in near shore and offshore bottom areas showed that 3,211
individuals of 47 species were recorded in both electrofishing (45 transects) and gill netting (26 net-nights)
samples. Electrofishing results indicated total numbers of fish captured were higher in the inflow (1,277)
than in the transition (934) or forebay (473) zones of the reservoir. Gizzard shad (32 percent) comprised
the majority of the total individuals collected, followed by emerald shiners (18 percent), bluegill (8 percent),
and skipjack herring (7 percent). Threadfin shad numbers were moderate in the transition (catch per unit
effort, CPUE=271 per 300m transect) and high in the forebay (CPUE^SS 1 per 300m transect) of Wheeler
Reservoir. Gill netting catch rates were slightly higher in the forebay (CPUE=30 per net night) than the
transition (CPUE=11 per net night) or the inflow (CPUE=14), due to much higher numbers of skipjack
herring in the forebay.
The Reservoir Fish Assemblage Index (RFA1) rated the littoral fish community (based on
electrofishing results) good in the forebay (RFAI=44) and inflow (RFAI=44) and fair in the transition
(RFA1=40). A high percentage of tolerant individuals (75 percent) and a lower average number of
individuals (62) influenced the fair rating in the transition. Indices, determined by gill netting, for the
transition and forebay zones of Wheeler Reservoir were 42 (good) and 40 (fair), respectively. Gill netting
RFA1 values were not calculated for inflow zones of run-of-the-river reservoirs due to low numbers of
replicate samples
Combined electrofishing and gill netting RFAI scores for the forebay (RFAI=42) and the
electrofishing RFAI for the inflow (RFAI=44) were rated good. The combined transition RFAI (RFAI=41)
ranked fair.
Electrofishing (15 transects) and gill netting (12 net-nights) results from the Elk River embayment
yielded 5,126 individuals of 30 species. Gizzard shad were the most abundant species, comprising 78
percent of the total number of fish sampled. Other species of interest were bluegill (8 percent) and
largemouth bass (2 percent). High numbers of gizzard shad accounted for the wide margin in catch rates
for both gear types (4,776 individuals in electrofishing and 350 for gill netting). Unusually high numbers of
young-of-year threadfin shad (3,356 per transect) were also observed in the electrofishing sample.
The Reservoir Fish Assemblage Index (RFAI) rated the quality of the littoral community (as
determined by electrofishing samples) good in the Elk River embayment (RFAI=42). Metrics receiving high
scores were number of species, and number of piscivorous, intolerant, and lithophilic spawning species.
The gill netting RFAI of 34 rated fair with metric values being somewhat evenly distributed throughout the
range of possible scores. The combined electrofishing and gill netting RFAI of 34 rated the Elk River
embayment of Wheeler Reservoir as fair.
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Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—No bacteriological studies were conducted at recreation sites in
Wheeler Reservoir in 1993 Fecal coliform bacteria concentrations at the monthly Vital Signs locations, the
forcbay, transition zone, and Elk River Embayment, were very low (geometric mean <20/100 ml). The
highest concentration for any sample was 219/100 ml in the transition zone in September.
Fish Tissue—Composite catfish samples for screening purposes were collected from the forebay,
transition zone, and inflow in autumn 1992. Intensive studies were also conducted during this same time
period to examine DDTr concentrations in a 20 mile stretch of Wheeler Reservoir near the Indian Creek
embayment, located between the inflow and the transition zone. Three five-fish composites of channel
catfish, largemouth bass, and smallmouth buffalo were collected from four locations for the intensive study.
Samples for screening purposes indicated all metals were low or not detected. DDTr was the only
pesticide detected with a range of 1.0 to 1.6 jig/g Relatively high PCB concentrations reported for 1990
(maximum 1.4 |ig/g) were again found in 1991 (maximum 1.3 |.ig/g) but generally lower levels were found
in 1992 (maximum 0.8 |ag/g). PCB concentrations during all years were higher at upstream locations.
Samples from the intensive study in 1991 found quite high concentrations of DDTr. At least one
sample of one test species exceeded 5 \xsjg at all four sites. Highest concentrations were in smallmouth
buffalo (maximum 43 (*g/g) from near the mouth of Indian Creek with lower concentrations at the
upstream location and the location at the downstream end of the study reach. Largemouth bass tended to
have lower concentrations than the other two species Samples for the intensive study in autumn 1992
(samples actually collected in January 1993) had substantially reduced concentrations. Only two samples
exceed 5 |.ig/g whereas 15 from 1991 exceeded that concentration. Also, the geographical pattern was not
distinct in these samples. Because of the discrepancy between the two years, the intensive study was
repeated in autumn 1993 but results were not available at the time this report was prepared.
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Tims Ford Reservoir
Summary of 1993 Conditions - Ecological Health
Water—The average flow through Tims Ford Reservoir in 1993 was about 86 percent of normal,
making the average residence time about 329 days The reservoir was strongly stratified with a maximum
temperature difference of 22.9°C in the water column at the forebay in July. Tennessee's maximum
temperature criterion for aquatic life is 30.5°C. July surface temperatures were 31,3°C at the forebay and
31 5°C at the mid-reservoir station, the only time the temperature criterion was exceeded. DO depiction
(DO <2.0 mg/1) began in May at the bottom of the water column at mid-reservoir, and in June in the
metalimnion at mid-reservoir and in the forebay in both the metahmnion and at the bottom. The two areas
of depleted DO expanded and met in July at mid-reservoir and September at the forebay. The extensive
area of depleted DO resulted in a poor DO rating for Tims Ford in the reservoir ecological health index. As
surface temperatures cooled in the early fall, the area of depleted DO declined as metalimnetic water mixed
with surface water Some extremely high DO concentrations occurred at the forebay in the upper part of
the metalimnion. Both June and July DO concentrations exceeded 15 mg/1.
Conductivities in Tims Ford Reservoir were the fifth highest of the 19 tributary reservoirs.
Conductivities were about 180 ^mhos/cm in April, increased throughout the year in the DO depicted
bottom waters to a maximum of 242 and 285 ^mhos/cm in October at the forebay and mid-reservoir,
respectively Conductivities declined in the DO supersaturated surface water in the summer to a minimum
of 145 ^mhos/cm at the forebay in July and 136 (amhos/cm in June at mid-reservoir. The waters in Tims
Ford are somewhat basic, as the minimum pH in April was 7.6 in the mid-reservoir In June, surface pH
was over 9.0 in both the forebay and mid-reservoir. The minimum pH was 6.8 at the bottom of the water
column in September in mid-reservoir.
Organic nitrogen concentrations in June were 0.30 and 0.38 mg/1 at the forebay and mid-reservoir,
respectively, and 0.22 and 0.43 mg/1 in August Nitrates were 0.30 and 0.76 mg/1 in April, declining to
<0.01 at both locations in August. Total nitrogen concentrations at mid-reservoir in 1993 was the second
highest concentration of the 33 tributary reservoir stations Total phosphorus concentrations were
0.01 mg/1 during both surveys at the forebay, and 0.02 and 0.005 mg/1 at mid-reservoir in April and
August, respectively. The TN/TP ratios were very high, ranging from 24 at the forebay to 90 at mid-
reservoir, both in August Dissolved ortho phosphorus concentrations were <0.002 mg/1 at both stations
during both surveys. Average total organic carbon concentrations in Tims Ford Reservoir were the fifth
highest of the 19 tributary' reservoirs. The minimum total organic carbon concentration was 2.6 mg/1 in
April, the maximum was 3.2 mg/1 in August, both at mid-reservoir
Chlorophyll a concentrations averaged 5 4 jj.g/1 at mid-reservoir and 4.3 (j.g/1 at the forebay. Some
of the highest DO concentrations were below the depth at which the chlorophyll composite was collected in
the forebay, thus the average sampled forebay concentration may be a little lower than actual values. The
chlorophyll concentrations rated good in the reservoir ecological health index Secchi depths varied from
1.3 meters in April to 5.5 meters in May at the forebay, and 1.3 meters in April to 8.0 meters in September
at mid-reservoir.
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Sediment Quality—Chemical analyses of sediments in Tims Ford Reservoir in 1993 indicated high
levels of nickel in the forebay (51 mg/kg). Elevated levels of un-ionized ammonia were also found in both
the forebay (230 (ig/1) and mid-reservoir (410 (ig/1) sediment samples. Toxicity tests detected acute toxicity
to daphrnds (5 percent survival) and rotifers (65 percent survival) in the mid-reservoir. Particle size
analysis showed sediments in the forebay were 99 percent silt and clay; and in the mid-reservoir were
55 percent silt and clay, and 45 percent sand.
Sediment quality ratings used in the overall Tims Ford Reservoir ecological health evaluation for
1993 were good at the forebay sampling site, rather than excellent due to nickel and ammonia; and poor at
the mid-reservoir sampling site (because of acute toxicity to daphnids and rotifers and presence of
ammonia).
Benthic Macroinvertebrates—Two sites were chosen for sampling the first year on Tims Ford
Reservoir, a forebay site and a mid-reservoir site of the Elk River arm. The forebay location had only 2
2
taxa and 122 organisms/m . Tubificidae accounted for 90 percent of the total. The inflow site had 108
2
organisms/m representing 12 species and was dominated by Chironomus sp (32 percent) and Branchiura
sowerbvi (27 percent). The forebay had a very poor benthic community, and scored poor on 5 of the 6
metrics, diversity, number of long-lived species, number of EPT species, proportion of the sample as
tubificids, and unevenness of the dominant species. The only metric to get a good score was the proportion
of the sample represented by chironomids. The inflow site rated only a little better than the forebay with a
poor benthic community. Low diversity, absence of long-lived species, and a disproportionate number of
the dominant taxa accounted for this site rating poor
Fish Assemblage—Shoreline electrofishing (30 transects) and offshore experimental gill netting
(24 net-nights) yielded 2,726 individuals with 32 species represented. The dominant species by number
included bluegill (50 percent), green sunfish (8 percent), spotfin shiners (7 percent), and brook silversides
(6 percent). Catch rates for most species (except for bluegill and green sunfish), utilizing both gear types,
were higher at the transition zone than the forebay.
The Reservoir Fish Assemblage Index (RFA1) rated the littoral fish community (based on
electrofishing results) fair in the forebay zone (RFAI=40) and good in the transition (RFAI=46) of Tims
Ford Reservoir. The transition received midrange to maximum scores for all metrics, except average
number of individuals per transect, resulting in a slightly higher rating than the forebay. Identical gill
netting scores for ten of the twelve metrics resulted in a good rating (RFAI=44) at both reservoir sample
zones. Combined electrofishing and gill netting RFAI scores rated both the forebay (RFAI=42) and the
transition (RFA1=45) zone good.
Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—The swimming area on Dry Creek and an area in Estill Springs Park
were tested for fecal coliform bacteria in 1993. Bacteria concentrations were low at Estill Springs Park,
geometric mean of 38/100 ml for all samples. In Dry Fork, bacteria concentrations were high in samples
collected within 24-hours of rainfall, geometric mean of 389/100 ml, but were within Tennessee criteria if
the rainfall samples were excluded, geometric mean of 151/100 ml.
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Fish Tissue—Channel catfish composites collected from the forebay and transition zone in autumn
1992 were screened for pesticides, PCBs, and selected metals. All analytes were either not detected or
found in only low concentrations. One point of interest was absence of PCBs in these samples because
previous screening studies had typically found PCBs, sometimes at slightly elevated levels.
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Elk River Stream Monitoring Site
Summary of 1993 Conditions - Ecological Health
Water—The water of the Elk River is moderately hard (average hardness of 130 mg/1) arid
moderately alkaline (average total alkalinit>\of 103 mg/1). The median pH for the stream monitoring site
was 7.7 The river was generally well oxygenated with dissolved oxygen levels ranging from 54 to 108
percent of saturation. Five of the six dissolved oxygen levels were above 85 percent of saturation. At the
lowest dissolved oxygen saturation level, the dissolved oxygen concentration was 5.4 mg/1.
Of the 12 streams monitored across the Tennessee Valley, the Elk River ranked among the highest
in average concentrations of total phosphorus (0.374 mg/1), dissolved orthophosphate (0.173 mg/1),
nitrate+nitrite-nitrogen (0.68 mg/1), ammonia nitrogen (0.042 mg/1). The high total phosphorus and
nitrate+nitrite-nitrogen concentrations yielded a poor rating for nutrients at the site.
Seven analyses for priority pollutant metals (dissolved cadmium, lead, nickel, silver, and zinc and
total and dissolved copper and zinc) were performed bi-monthly Dissolved cadmium (5 of 6 samples) and
total zinc (2 of 6 samples) were detected but neither exceeded EPA guidelines for the protection of aquatic
life or human health.
Sediment—Sediment quality rated good in 1993 with no acute toxicity observed and no metals,
PCBs, or pesticides exceeding the EPA guidelines. This is an improvement over 1992 when the sediment
quality rated only fair.
Benthic Macromvertebrates—In 1993, benthic macroinvertebrate results rated fair with a
2
Modified Benthic Index of Biotic Integrity (MBIBI) score of 39, with 73 taxa and 2,384 organisms/m .
2
Conditions in 1992 rated poor (MBIBI score 27) with 52 taxa and 2,454 organisms/m The benthic fauna
improved one classification since 1992. Dominant organisms in 1993 were dipteran midge larvae
(69 percent), coleopteran riffle beetles (8 percent), and caddisflies (7 percent). Dipteran midge larvae were
also the most dominant organism in 1992 (70 percent), followed by nutrient tolerant oligochaeta worms
(18 percent) and coleopteran riffle beetles (5 percent). Siltation from agricultural land usage along the river
and unstable substrates are a serious problem affecting benthic organisms at this site.
Fish Community Assessment—Fish community was not evaluated in the Elk River in 1993.
Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—The canoe access location at Garner Ford on the Elk River, about one
and one-half miles downstream of Tims Ford Dam, was tested for fecal coliform bacteria in 1993. Five of
the 12 samples were collected within 48-hours of rainfall of at least one-half inch Bacteriological water
quality for samples collected more than 24-hours after rainfall easily met the Tennessee water quality
criterion for recreation, but rainfall samples greatly exceeded criterion.
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Fish Tissue—Smallmouth Buffalo, channel catfish, and spotted bass were collected in summer
1992. One five fillet of each species was analyzed for selected metals, pesticides, and PCBs. All analytes
were either not detected or found in low concentrations.
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GUNTERSVILLE RESERVOIR - SEQUATCHIE RIVER WATERSHED
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Guntersville Reservoir
Summary of 1993 Conditions - Ecological Health
Water—During the summer of 1993, Guntersville Reservoir was well mixed and exhibited only
weak thermal stratification. Surface water temperatures ranged from 16.2°C in April to 30.5°C in July at
the forebay and from 15.1°C to 30.9°C for the same months at the transition zone. Temperatures above
30.0°C exceed the state of Alabama's water quality criteria for fish and aquatic life.
Values for DO at the 1.5m depth ranged from 10.1 mg/l in April to 6.5 mg/1 in September at the
forebay and from 9 3 mg/1 in April to 5 .6 mg/1 in August at the transition zone At the inflow sampling
station site (i.e. the tailrace ofNickajack Dam) a minimum DO of 1.8 mg/1 was recorded in July. The State
of Alabama's minimum dissolved oxygen criteria for the protection of fish and aquatic life is 5.0 mg/1,
measured at the 1.5 meter depth.
Summer (April-September) temperature data for the forebay depict weak thermal stratification in
the downstream portion of Guntersville Reservoir in 1993. Maximum surface to bottom temperature
differentials
(AT's = 3.3°C) occurred at the forebay in May and June. However, June and July showed the development
of a oxycline in the forebay, with surface DO's being 5.5 and 6.3 mg/1, respectively, greater than bottom
DO's The minimum DO measured in Guntersville reservoir in 1993 was 0.6 mg/1 at the bottom in July in
the forebay, however, this apparently persisted for only a short period of time and by August bottom DO's
were back up to 5 mg/I
The transition zone was well mixed throughout the summer with maximum AT's (2.2°C) and
ADO's (3.4 mg/1) occurring in June. One interesting observation was the very warm temperatures which
existed throughout the water column at the transition zone in July, when surface temperatures were 30.9°C
and bottom temperatures were 30.0C. The minimum DO measured at the transition zone was 5.5 mg/1 at
the bottom in July
The very low DO concentration of 1.8 mg/1, measured in July in the tailrace below Nickajack Dam
(i.e., the inflow site), was the lowest ever recorded in the releases from Nickajack Dam. In addition,
releases of water from Nickajack Dam were consistently below Alabama's DO water quality criteria for the
protection of fish and aquatic life of 5.0 mg/1 (at the 1.5 meter depth) in July, potentially impacting the
ecological health of the inflow site on Guntersville Reservoir.
These data resulted in DO ratings used in the overall reservoir ecological health evaluation for
Guntersville Reservoir to be good at the forebay (minor hypolimnetic anoxia); excellent at the transition
zone, and very poor at the inflow (due to low DO's in the releases from Nickajack dam).
Values of pH ranged from 6.9 to 8 3 Surface water pH values in excess of 8.5 (Alabama's pH
water quality criteria for the protection of fish and aquatic life of 8.5) were not observed in Guntersville
Reservoir in the summer of 1993.
At the forebay, the highest chlorophyll a concentration of 9 ^g/1 was measured in July (average
summer chlorophyll a concentration was 5-6 (ig/I in 1993). At the transition zone chlorophyll a
concentrations were lower, averaging about 4 jag/1 TN/TP ratios frequently exceeded 20 at both the
forebay and transition zone, indicating conditions when phosphorus concentrations may have limited
photosynthesis
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The chlorophyll a ratings used in the 1993 ecological health evaluation for Guntersville Reservoir
were good at both the forebay and the transition zone (i.e., average concentrations between 3 and 10 ng/1).
Historically, water clarity on Guntersville Reservoir has been among the highest of the mainstem
Tennessee River reservoirs. In 1993, at the forebay and transition zone, respectively, average Secchi depth
was 1.8 and 1.6 meters, total suspended solids was 3.7 and 3.2 mg/1; and true color was 8.3 and 7.1 PCU.
Sediment—Chemical analyses of sediment in Guntersville Reservoir in 1993 indicated the presence
of chlordane (15 (ig/g) in samples collected at the forebay. Toxicity tests did not reveal acute toxicity to
daphnids or rotifers from the two sites tested (i.e. forebay and transition zone). Particle size analysis
showed sediments from the forebay were 98 percent silt and clay; and from the transition zone were
39 percent silt and clay, 61 percent sand.
Sediment quality ratings used in the overall Guntersville Reservoir ecological health evaluation for
1993 were good at the forebay (presence of chlordane); and excellent at the transition zone.
Benthic Macromvertebrates—The forebay site had a good benthic macroinvertebrate community,
the transition zone had an excellent benthic community, and the inflow had a fair benthic community. The
2
forebay had 20 taxa and 772 organisms/m with Coelotanvpus tricolor (27 percent) and Corbicula
2
fluminea (18 percent) as the dominant taxa. The transition zone had 1340 organisms/m representing 38
taxa, the dominant taxa were Corbicula fluminea (26 percent) and Coelotanvpus tricolor (17 percent). The
2
inflow site had 35 taxa and 672 organisms/m with Corbicula fluminea (39 percent) and Tubificidae
(24 percent) as the dominant taxa
The forebay site fell short of an excellent rating primarily because high numbers of chironomids
and a mediocre EPT community. All other metrics were excellent. The transition zone scored excellent, and
fell just short of perfect because the percentage of the community made of chironomids was slightly
elevated The absence of adequate long-lived taxa, depressed diversity and EPT taxa, and unevenness of the
dominant organisms all contributed to the inflow site receiving a fair rating. Metrics which rated food at the
inflow were (due to their relatively low numbers) were tubificids and chironomids.
Aquatic Macrophytes—Aquatic macrophytes on Guntersville Reservoir increased from 5,993
acres in 1992 to 7,613 acres in 1993. The reservoir had the largest acreage of aquatic plants in the TVA
system. About 99 percent of the total amount of vegetation was upstream of TRM 363 and primarily
confined to shallow embayments and overbank areas adjacent to the river channel. Eurasian watermilfoil
was the dominant submersed macrophyte species and colonized about 6,500 acres in 1993. About three
acres of "topped out" hydrilla occurred on Guntersville Reservoir in 1993 compared to about 2,900 acres in
1988 when aquatic vegetation coverage peaked at about 20,200 acres. In 1990, the reservoir was stocked
with 100,000 triploid grass carp for aquatic vegetation control.
Fish Assemblage—Shoreline electrofishing (45 transects) and offshore gill netting (29 net-nights)
produced 8,441 fish representing 41 species. Both sampling techniques indicated higher catch rates in the
forebay than the other two zones of the reservoir. Gizzard shad (19 percent) was the dominant species,
followed by bluegill (17 percent), and emerald shiners (14 percent). Results indicated that largemouth bass
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(4 3 percent) was the only major sport fish species to comprise more that one percent of the electrofishmg
sample. As in previous years, largcmouth bass were five times more abundant in the transition zone than
either of the other two zones.
Electrofishing RFAI analysis determined that fish communities in both the inflow (RFAI=30) and
transition zone (RFAI=28) rated poor, while that present in the forebay zone (RFAI=38) rated fair.
Compared to other mainstream reservoirs, the Guntersville inflow and transition zones were in the lower
third and the forebay zone the upper third. The poor designation of the transition also represented a
significant decrease from the good rating in 1992. Metrics contributing to the poor designation for the
inflow and transition areas were low numbers of sucker and intolerant species, depressed fish abundance,
and high percentages of anomalies. Gill netting results showed both zones to be fair (transition RFAI=34
and forebay RFAI=38). Transition zone scores were midrange (most metrics received a score of three),
while forebay scores tended to be very low or very high (metrics received a score of one or five) for most
metrics. Gill netting RFAI values were not calculated for inflow zones of run-of-the-river reservoirs due to
low numbers of replicate samples.
Combined electrofishing and gill netting RFAI values for both the forebay (RFAI=38) and
transition (RFAI=31) were classified as fair, followed by the electrofishing RFAI for the inflow (RFAI=30)
which was poor.
Summary of 1993 Conditions - Use Suitability
Fecal Cohform Bacteria—Two swimming beaches, one boat ramp, the middle of the channel
under five causeways, both Vital Signs locations, and an area downstream of Guntersville sewage
treatment plant were each tested twelve times in 1993 for fecal coliform bacteria. No samples were
collected within 48-hours of a rainfall of one-half inch or greater. The sampled swimming beaches were the
Camp Barber Boy Scout Camp, and the Camp Trico Girl Scout Camp.
The 1993 survey at the causeways was intended to identify the watersheds having the most
potential for affecting the bacteriological water quality in the main channel of Guntersville Reservoir. The
other sites were selected to determine the impacts discharges or runoff from urban areas have on
Guntersville Reservoir. At all but two sites, the bacteria concentrations were very low (geometric means
<20/100 ml). At the Polecat Creek Causeway and at the Crow Creek boat ramp the fecal coliform bacteria
samples had geometric mean concentrations of 69 and 67/100 ml, respectively. The lack of rainfall during
the sampling period may have resulted in lower concentrations at some sites. For the regular monthly Vital
Signs sampling, all fecal coliform concentrations were very low.
Fish Tissue—Composite catfish samples were collected from the forebay, transition zone, and near
the inflow in autumn 1992. One reason for resampling was that relatively high PCB concentrations of
chlordane and PCBs had been found in 1990 (chlordanc levels at the forebay were 0.10 (ig/g and those
from near the inflow were 0.11 ja.g/g, whereas, PCB concentrations at these two locations were 1 2 and
1.3 (ag/g, respectively). Chlordane was not detected in any of the 1992 samples and PCB concentrations
decreased progressively from year to year (maximum 0.9 (ag/g in 1991 and 0.4 ng/g in 1992). Other
pesticides and metals were relatively low during all years at all locations.
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Sequatchie River Stream Monitoring Site
Summary of 1993 Conditions - Ecological Health
Water—The water of the Sequatchie River is moderately hard (average hardness of 90 mg/l) and
moderately alkaline (average total alkalinity of 74 mg/l). The median pH for the stream monitoring site was
7.4. The river was well oxygenated with dissolved oxygen levels ranging from 72 to 93 percent of
saturation.
Of the 12 streams monitored across the Tennessee Valley, the Sequatchie River ranked among the
highest in average concentrations of organic nitrogen (0.372 mg/l) and ammonia nitrogen (0.090 mg/l). It
was among the lowest in average total phosphorus with a concentration of 0.022 mg/l. The average
nitrate+nitrite-nitrogen (0.42 mg/l) and average dissolved orthophosphate (0.009 mg/l) concentrations
ranked mid-way of all station medians. The low average total phosphorus and acceptable nitrate+nitrite-
nitrogen concentrations yielded a good rating for nutrients at the site.
Seven analyses for priority pollutant metals (dissolved cadmium, lead, nickel, silver, and zinc and
total and dissolved copper and zinc) were performed bi-monthly. Dissolved cadmium was detected in 4 of 5
samples. However, the concentrations did not exceed the EPA guideline for the protection of aquatic life or
human health. Additional metals analyses included total and dissolved forms of iron and manganese. Total
iron (2 of 6 samples) and total manganese (1 of 6 samples) exceeded the EPA guideline for combined
consumption of fish and water.
Sediment—Sediment quality rated good in 1993 with no acute toxicity observed and no metals,
PCBs, or pesticides exceeding the EPA guidelines The sediment quality also rated good in 1992.
BenthicMacroinvertebrales—In 1993, benthic macroinvertebrate results were rated fair with a
J
Modified Benthic Index of Biotic Integrity (MBIBI) score of 44, with 80 taxa and 3,951 organisms/m
Conditions in 1992 also rated fair (MBIBI score 41) with 93 taxa and 2,096 organisms/m . Dominant
organisms in 1993 were dipteran midge larvae (38 percent), caddisflies (27 percent), and mayflies
(12 percent). Nutrient tolerant oligochaete worms were the dominant group in 1992 (22 percent), followed
by dipteran midge larvae (20 percent) and caddisflies (16 percent). Conditions have improved between
sampling years The fair rating (score 44) given for 1993 is borderline good for this site; however, siltation
from agricultural land use along the river and coal mining in the Sequatchie watershed continues to impact
benthic communities in the river
Fish Community Assessment—No change was seen as the fish community rated fair with an Index
of Biotic Integrity (IBI) score of 42 during both 1993 and 1992. Problems continued to occur in species
richness and composition and in fish density. Forty-six to 69 native fish species were expected at this
station, but only 38 were found This loss of diversity was most noticeable among darters and intolerant
species Fish density was one of the lowest found at the 11 stations sampled in 1993. Poor conditions
observed at this station were sedimentation of shoreline habitats and occasional bank erosion.
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Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—Four canoe access sites on the Sequatchie River from river mile 35.6 to
51.3 were tested for fecal coliform bacteria twelve times each in 1993. Two samples were collected within
48-hours of a rainfall greater than one-half inch. The geometric mean of fecal coliform bacteria
concentrations for all samples at the four sites ranged from 43 to 103/100 ml, all well within the Tennessee
bacteriological criterion for recreation. Concentrations were higher in the two rainfall samples.
Fish Tissue—Five freshwater drum, channel catfish, and largemouth bass were collected from the
Sequatchie River during summer 1992. Composited fillets for each species were analyzed for selected
metals, pesticides, and PCBs. Most analytes were not detected. Those that were had low concentrations.
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NICKAJACK RESERVOIR - CHICKAMAUGA RESERVOIR WATERSHED
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Nickajack Reservoir
Summary of 1993 Conditions - Ecological Health
Water—Surface water temperatures during the April to September monitoring period ranged from
a 17.6°C in April to 29.2°C in July at the forcbay; and DO at the 1.5m depth ranged from 5.6 mg/1 in
August to 10.2 mg/1 in April at the forebay. At the inflow sampling station site (i.e., the tailrace of
Chickamauga dam) a minimum DO of 2.2 mg/1 was recorded in July. Tennessee's minimum dissolved
oxygen criteria for the protection of fish and aquatic life is 5.0 mg/1, measured at the 1.5 meter depth.
The riverine character of Nickajack Reservoir, with an average hydraulic residence time of only
three to four days, results in it being the best mixed of any of the Vital Signs reservoirs. Temperature data
reflect a lack of thermal stratification in Nickajack Reservoir in 1993. A maximum surface to bottom
temperature differential of 1.8°C was measured at the forcbay in May. However, summer DO data reflect a
small oxycline in the forebay of Nickajack Reservoir when surface to bottom DO differentials were 3 .0,
3 1, 4.8, and 2.1 mg/1, respectively, from May through August. The drought like conditions and low flows
also depressed concentrations of oxygen. For example, minimum oxygen concentrations measured at the
bottom in the forebay ofNickajack Reservoir were 4.6, 4.7, and 5 0 mg/1, respectively, for 1990, 1991, and
1992. However, in 1993, minimum DO concentrations at the bottom in the forebay ofNickajack Reservoir
were 3.0 mg/1 In addition, in late July (between the mid-July and mid-August field surveys), releases from
Nickajack Dam were recorded as low as 1.8 mg/1, indicating a short period when DO concentrations in the
hypolimruon of the forebay were less than 2 mg/1. Also in July, DO's as low as 2.2 mg/1 and frequently in
the mid-3's mg/1 were measured in the releases from Chickamauga dam (i.e., the inflow to Nickajack
Reservoir).
Because DO concentrations were frequently below Tennessee's minimum dissolved oxygen criteria
for the protection of fish and aquatic life (5 0 mg/1 at the 1.5 meter depth), the DO rated poor at inflow
sampling site in the overall ecological health evaluation ofNickajack Reservoir. Based on no DO's actually
being measured in the hypolimnion of the forebay ofNickajack Reservoir below 2 mg/1, the forcbay
sampling site's DO rating was excellent.
Values of pH varied over a rather narrow range, from 7.0-8.0 during the summer of 1993. At the
forebay, the highest chlorophyll a concentration of about 10 p.g/1 was measured in May and averaged about
6 p.g/1 in the summer of 1993 Consequently, the chlorophyll a rating used in the 1993 ecological health
evaluation for Nickajack Reservoir was good (i.e., average concentration between 3 and 10 fj.g/1).
Sediment—Chemical analyses of sediments in Nickajack Reservoir in 1993 indicated the presence
of chlordane (21 |ig/g) from the forebay. Toxicity tests did not reveal acute toxicity to daphnids or rotifers
from the forebay Particle size analysis showed sediments from the forebay about 92 percent silt and clay.
The sediment quality rating used in the overall Nickajack Reservoir ecological health evaluation for
1993 was good (rather than excellent because chlordane was detected.
Benthic Mcicromvertebrates—Both the forcbay and inflow sites on Nickajack had excellent
benthic macroinvertebrate communities, an improvement from the previous vears. The forcbav site had 21
2
taxa and 535 organisms/m with Hexagenia limbata comprising 30 percent of the total. The inflow site
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2
had 38 taxa and 1458 organisms/m ; Cheumatopsvche sp and Tubificidae were dominant, comprising 22
and 19 percent of the total organisms present, respectively.
The forebay site fell short of a perfect score due to a slightly elevated chironomid community, but
still received an excellent rating. All other metrics were perfect. The inflow site scored perfect for each
metric evaluated, resulting in an excellent bcnthic community evaluation.
AquaticMacrophytes—Aquatic plants on Nickajack Reservoir increased from 583 acres in 1992
to 1,000 acres in 1993. Eurasian watermilfoil and spiny leaf naiad were the dominant species and occurred
in mixed colonies or occasionally with other species such as American pondweed and southern naiad.
Aquatic macrophytes were most abundant from TRM 425 upstream to TRM 440.
Fish Assemblage—Fish collections in the littoral (30 electrofishing transects) and offshore/benthic
areas (16 net-nights) of Nickajack Reservoir found fish to be more concentrated in the inflow zone (2,181)
than the forebay (1,337) particularly as indicated by electrofishing results. Although gill netting effort was
reduced in the inflow, catch per unit effort (CPUE) was similar between forebay and inflow zones. Bluegill
was the most abundant species (29 percent), followed by emerald shiners (20 percent). The majority of the
forage base in the Nickajack sample was comprised of several shiner species (golden, emerald, spotfin, and
steelcolor) instead of shad, which is unusual for run-of-the-river reservoirs.
The Reservoir Fish Assemblage Index (RFAI) rated the littoral fish (based on electrofishing
results) excellent in the inflow (RFAI=52) and fair in the forebay (RFAI=40) zones of Nickajack
Reservoir. The inflow index of 52 was the highest score observed for run-of-the-river reservoir inflows and
received maximum scores for all metrics except number of piscivorous, sucker, and intolerant species, and
percent anomalies The gill netting RFAI rated the forebay good (RFAI=48). Gill netting RFAI values were
not calculated for inflow zones of run-of-the-river reservoirs due to low numbers of replicate samples.
The combined electrofishing and gill netting RFAI score for the forebay (RFAI=44) was
determined to be good. The electrofishing RFAI for the inflow (RFAI=52) was rated excellent. High inflow
RFAI indices in 1992 and 1993 indicate Nickajack to have possibly the best fish community among run-of-
the-river inflows.
Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—Four swimming beaches and a boat ramp near Nickajack Dam, and one
boat ramp and two informal swimming areas in the North Chickamauga Creek Embayment were tested for
fecal coliform bacteria twelve times each in 1993 Two samples at each site were collected within 48-hours
of a rainfall of at least one-half inch. The geometric mean of the bacteria concentrations were very low
(<20/100 ml) at five of the eight sites. The geometric means at one formal and one informal swimming area
was 49 and 31/100 ml, well within Tennessee water quality criterion for recreation. At Smith's Camp-On-
The-Lake boat ramp, the geometric mean was 657/100 ml All the Vital Signs monthly samples at the
forebay were 10/100 ml or less.
Fish Tissue—The PCB concentration in channel catfish has averaged about 1.0 (ig/g over the last
three years. The TDEC has issued a precautionary advisory due to PCB contamination in catfish from
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Nickajack Reservoir This means that children, pregnant women, and nursing mothers should not consume
catfish, and all others should limit consumption to 1.2 pounds per month.
Fish tissue studies conducted in autumn 1992 were aimed at examining the long-term trend of PCB
concentrations in channel catfish and developing a data base for carp. Ten individuals of both species were
collected at two sites, one near the forebay, and the other in the upper end of the reservoir about 13 miles
downstream of the inflow. The 1992 study also included collection of striped bass (including hybrid striped
bass x white bass) from just downstream of Chickamauga Dam. PCB concentrations in the catfish and carp
were substantially reduced (about half) from those previously found. The average for channel catfish was
0.4 and 0.5 (ig/g (maximum 0.8 (ig/g) at the forebay and upper location, respectively. Concentrations in
carp were similar to those in catfish Highest concentrations were found in striped bass (average 0.8 (ig/g
and maximum 1.1 |ig/g). The reduced concentrations in catfish and carp need to be verified, so these
species, along with striped bass, were resampled in autumn 1993. Results were not available at the time
this report was prepared.
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Chickamauga Reservoir
Summary of 1993 Conditions - Ecological Health
Water—During the April-September 1993 monitoring period, coolest surface water temperatures
in Chickamauga Reservoir were in April and the warmest in July. Surface temperatures ranged from a
minimum of 17.0°C to a maximum of 31 7°C at the forebay; from 16.2°C to 30.1°C at the transition zone;
and from 19.1°C to 28.8°C in the Hiwassee River embayment. Tennessee's maximum water temperature
criteria for the protection of fish and aquatic life is 30.5°C.
Dissolved oxygen (DO) concentrations at the 1.5m depth ranged from a low of 6.9 mg/1 in
September to a high of 11.4 mg/1 in April at the forebay; from 5.7 mg/1 in September to 10.3 mg/1 in April
at the transition zone; and from 7.3 mg/1 in August to 9.9 mg/1 in April at the sampling location in the
Hiwassee River embayment. At the inflow sampling site (i .e., the tailrace of Watts Bar dam) a minimum
DO of 3.7 mg/1 was recorded in August. Tennessee's minimum dissolved oxygen criteria for the protection
of fish and aquatic life is 5 .0 mg/1, measured at the 1.5 meter depth.
Temperature data depict seasonal warming and weak thermal stratification in Chickamauga
Reservoir from May through July. The maximum observed surface to bottom temperature differentials
(AT's), occurred in July. AT's were 5.5°C at the forebay, 3.2°C at the transition zone, and 4.1°C in the
Hiwassee River embayment. There was also an oxycline at the forebay and transition zone in June and July
when differences between surface and bottom DO's (DO's) were about 6 to 9 mg/1 at the forebay and
transition zone. In July 1993, a minimum DO of less than 0.1 mg/1 was measured on the bottom at the
forebay and a minimum of 1.6 mg/1 was measured on the bottom at the transition zone. Better DO
conditions were observed in the Hiwassee River embayment portion of Chickamauga Reservoir, where
maximum DO's were only 1.7 mg/1 and near bottom DO's only slightly below 6 mg/1
DO ratings used in the overall reservoir ecological health evaluation for Chickamauga Reservoir
were good at the forebay; good to excellent at the transition zone, excellent in Hiwassee River embayment;
and fair at the inflow. The forebay would have rated higher had it not been for the low near bottom oxygen
concentrations which existed in July The fair rating at the inflow sampling site on Chickamauga Reservoir
was a result of oxygen levels being measured about 1.5 mg/1 below the Tennessee criteria (5 mg/1, at the
1.5 meter depth) in the releases from Watts Bar dam.
Values of pH ranged from 6.8 to 8.8 on Chickamauga Reservoir, in 1993. Near surface pH values
exceeding 8.5 (and DO saturation values exceeding 100 percent) were observed on only two occasions
(April and July), both at the forebay. Both of these periods of high pH and high oxygen saturations were
also coincident with high chlorophyll a concentrations, indicative of periods of high photosynthetic activity
Tennessee's maximum pH criteria for the protection of fish and aquatic life is 8.5.
Total nitrogen (TN), total phosphorus (TP), and dissolved ortho phosphorus (DOP) were low in
the Tennessee River portion of Chickamauga Reservoir in 1993. TN averaged only 0.37 mg/1 at the
forebay, the lowest TN concentration measured at any of the Tennessee River sampling sites in 1993. At
both the forebay and the transition zone, TP and DOP concentrations averaged only about 0.026 mg/1 and
0.005 mg/1, respectively, and were among the lowest TP and DOP concentrations measured at any of the
Tennessee River sampling sites in 1993 Because of these low concentrations (and because TN/TP ratios
often exceeded 20), periods of phosphorus limitation on algal productivity were likely to have occurred.
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In 1993, Chickamauga Reservoir chlorophyll a concentrations averaged 8.5 fj.g/1, 7.8 (ig/1, and
5.5 pg/1, respectively, at the forebay, transition zone, and Hiwassee River embayment. Consequently, the
chlorophyll a ratings used in the 1993 ecological health evaluation for Chickamauga Reservoir were good
(i.e., falling in the 3 to 10 fag/1 range) at all three locations.
Sediment Quality—As in 1990, 1991, and 1992, chemical analyses of sediments from
Chickamauga Reservoir in 1993 found high levels of copper (64 mg/kg) and zinc (320 mg/kg) in the
forebay. High levels of copper (50 mg/kg) were also found in the Hiwassee River embayment, which was
sampled for the first time in 1993. Chlordane was also detected in the forebay (16 (ag/g) and the transition
zone (15 |ig/g). Toxicity tests indicated no acute toxicity to either species from the three sites tested, but
survival of rotifers (75 percent survival) was reduced in the transition zone. Toxicity to rotifers was
detected in both forebay and transition zone samples in 1992. Particle size analysis showed sediments from
the forebay were 97 percent silt and clay; from the transition zone were 86 percent silt and clay, 14 percent
sand; and from the Hiwassee River embayment were 63 percent silt and clay, 37 percent sand
Sediment quality ratings used in the overall Chickamauga Reservoir ecological health evaluation
for 1993 were fair at the forebay (presence of copper, zinc and chlordane), fair at the transition zone
(presence of chlordane and reduced survival of rotifers); and, good in the Hiwassee River embayment
(presence of copper).
Benthic Macroinvertebrates—The forebay and transition zone sites had excellent benthic
communities, and the inflow site was fair. The Hiwassee embayment, a major component of Chickamauga
Reservoir, was also included in the ecological health rating. It was shown to support a good benthic
community. The forebay site had 19 taxa and 847 organisms/m . The most numerous taxa collected were
the chironomid Coelotanvpus sp (29 percent), the mayfly Hexagenia limbata (20 percent), the asiatic clam
Corbicula fluminea (19 percent) and Tubificidae (17 percent). The transition zone was represented by 25
2
taxa and 897 organisms/m with Hexagenia limbata comprising 26 percent of the total organisms and
2
Tubificidae comprising 18 percent of the total organisms. The inflow had 21 taxa and 845 organisms/m .
Gammarus fasciatus. an amphipod, was the dominant species present comprising 36 percent of the total
organisms. The Hiwassee embayment had the greatest diversity and abundance of organisms than any other
2
site on Chickamauga Reservoir. It had 2312 organisms/m representing 49 species; Tubificidae were the
dominant taxa collected (36 percent) followed by the snail Musculium transversum (17 percent).
The forebay on Chickamauga supported an excellent benthic community, however, the overall
benthic score was lowered due to an elevated chironomid community and lowered EPT community. The
transition zone also received an excellent rating but fell short of perfect because of an elevated chironomid
community and lowered numbers of long-lived taxa. The inflow site rated fair primarily because of an
absence of long-lived organisms such as Corbicula sp and Hexagenia sp, and because of reduced diversity
and EPT taxa present. The Hiwassee embayment supported a good benthic community in 1993 because of
an excellent EPT representation, diversity, low numbers of Chironomids, and evenness of the dominant
species. An abundance of tubificids and a lack of long-lived species contributed to this site receiving a good
rating instead of an excellent rating.
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Aquatic Macrophytes—Coverage of aquatic macrophytes increased from 387 acres in 1992 to
1.185 acres in 1993. Most macrophytes were in Dallas Bay embayment and in small embayments and
overbank habitat upstream of TRM 499. Aquatic macrophytes on Chickamauga Reservoir peaked at about
7,500 acres in 1988 and continuously declined until 1993 when coverage increased. Spinylcaf and southern
naiad were the dominant species in 1993 although small colonies of Eurasian watermilfoil, American
pondweed, and American lotus also were present.
Fish Assemblage—Fish data collected in littoral (45 electrofishing transects) and offshore zones
(28 net-nights) of the forebay resulted in the collection of 44 species (6,994 individuals). Emerald shiner
was the most abundant species (collected at the rate of 56 per 300 meter electrofishing transect),
accounting for 36 percent of the total number of fish collected. Gizzard shad comprised 16 percent of the
sample, followed closely by bluegill at 14 percent. Electrofishing results showed approximately twice as
many individuals in the inflow (2,624) and transition (2,300) zones as the forebay (1,229), due to numbers
of gizzard shad and bluegill in the sample Numbers of YOY threadfin shad followed a similar pattern with
high catch rates in the forebay (CPUE=810 per 300m transect) and transition (CPUE=1,707 per 300m
transect) and very high catch rates in the inflow zone (CPUE=3,559 per 300m transect). Gill netting fish
abundance was higher in the transition (454) than the forebay (229); although abundance at the inflow zone
(158) was lower because of reduced effort, catch rate was similar to the transition zone.
The Reservoir Fish Assemblage Index (RFAI) rated the littoral fish community (based on results of
electrofishing samples) fair in the forebay (RFA1=32), good in the transition (RFAI=46), and excellent in
the inflow (RFAI=52) zones of Chickamauga Reservoir. The inflow index of 52 was the highest score
observed for run-of-the-river reservoir inflows and received maximum scores for all metrics except number
of sucker and tolerant species, dominance by a single specie, and percent anomalies. In 1992 the inflow
rated only fair (RFAI=34).
The gill netting RFAI rated the transition zone excellent (RFAI=52) and the forebay fair
(RFAI=36) The excellent score of 52 in the transition zone was the second highest ever observed for run-
of-the-river reservoirs and resulted from maximum scores for all metrics except number of sucker,
intolerant, and lithophilic spawning species, and percent insectivores. Gill netting RFAI values were not
calculated for inflow zones of run-of-the-nver reservoirs due to low numbers of replicate samples.
The combined electrofishing and gill netting RFAI score for the transition (RFAI=49) and forebay
(RFAI=34) were rated good and fair, respectively The electrofishing RFAI for the inflow (RFAI=52) zone
received an excellent rating, which was one of the highest scores for all inflows sampled in 1993.
Combined fish samples in shoreline electrofishing (15 transects) and offshore gill netting (12 net-
nights) produced a total of 2263 individuals including 31 species in the Hiwassee River embayment of
Chickamauga Reservoir The three most abundant species were redear sunfish (29 percent), gizzard shad
(19 percent), and bluegill (16 percent) There were six times as many fish collected by electrofishing as gill
netting, largely attributed to high numbers of sunfishes inhabiting shoreline areas
The electrofishing RFAI score of 36 rated the embayment community as fair and gill netting results
indicated good (RFAI=50) fish community conditions. Combining RFAI scores (RFAI=43) rated the Hiwassee
River embayment good (scoring criteria for run-of-the-river transition was used to obtain RFAI ratings). Metrics
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for both electrofishing and gill netting that influenced the high scoring included low percent dominance by a single
species, low percent omnivores, and high numbers of lithophilic spawning species.
Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—No bacteriological studies were conducted at recreation sites in
Chickamauga Reservoir in 1993. Fecal coliform bacteria concentrations at the monthly Vital Signs
locations, the forebay, transition zone, and Hiwassce River Embayment, were all 10/100 ml or less except
for one sample The April sample in the Hiwassee River Embayment had a concentration of 300/100 ml.
Fish Tissue—There are no fish tissue consumption advisories in effect for Chickamauga
Reservoir. Samples for screening studies were conducted in autumn 1991 and 1992. Fillets from five
channel catfish were collected from the inflow, transition zone, and forebay, composited by site, and
examined for a broad array of analyses (selected metals, pesticides, and PCBs on the EPA priority
pollutant list). Results from samples collected from all locations in 1991 had low or nondetectable levels of
metals and pesticides. PCB concentrations were 0.4, 0.7, and 1.2 (ig/g at the forebay, transition zone, and
inflow, respectively. This general trend had been documented in several previous studies but not always as
pronounced as in the 1991 results. Such was the case for 1992 results - PCB concentrations were 0.6, 0.7,
and 0.7 f^g/g at the forebay, transition zone, and forebay, respectively. All other analytes were not detected
or found in low concentrations in the 1992 fish samples.
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HIWASSEE RIVER WATERSHED
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Hiwassee Reservoir
Summary of 1993 Conditions - Ecological Health
Water—The average flow through Hiwassee Reservoir was about 107 percent of normal and the
average residence time was about 99 days. The reservoir was strongly stratified with a maximum
temperature difference in the water column at the forebay of 20.9°C in July. The maximum surface
temperature was 28.7°C in July, both at the forebay and mid-rescrvoir. North Carolina's standard for
maximum temperature of Class C waters is 29°C. Low DO water (DO <5.0 mg/1) first appeared at mid-
reservoir in June and at the forebay in July at the bottom of the water column at both locations. Depleted
DO water (DO < 2 .0 mg/1) occurred at both locations at the bottom of the water column in August and
September. The limited area of DO depiction provided ratings for the reservoir ecological health index of
fair at the forebay and good at mid-reservoir.
Conductivities averaged about 30 ^mhos/cm in April, increased slightly in the DO-depleted area to
a maximum of 40 and 38 pmhos/cm at the forebay and mid-reservoir, respectively The average
conductivity in Hiwassee Reservoir was the fourth lowest of the 19 tributary reservoirs. Only in June, July,
and August did pH reach or exceed 8.4, and only in the four to eight meter depth. Summer DO
concentrations were normally higher at these depths.
The organic nitrogen concentration, in April and August respectively, was 0.12 and 0.26 mg/1 at
the forebay, and 0.14 and 0 09 mg/1 at mid-rescrvoir. The April nitrate-nitrogen concentration was 0.12
and 0.10 mg/1 at the forebay and mid-rescrvoir, respectively. The August concentrations were <0.01 mg/ at
both locations. Total phosphorus concentrations were 0.007 mg/1 in April and 0.002 mg/1 in August at both
locations. Dissolved ortho phosphorus concentration was 0.01 mg/1 in April at mid-reservoir, and otherwise
<0.002 mg/1.
These low concentrations of nutrients resulted in low concentrations of total organic carbon and
chlorophyll and high water clarity Total organic carbon concentrations were 0.9 mg/1 in April and
approximately double that in August at both locations. Chlorophyll a concentrations averaged 2.2 pg/1 at
the forebay (third lowest of 19 tributary reservoir forcbays) and 3.7 jj.g/1 at mid-reservoir. The chlorophyll
concentrations rated fair at the forebay and good (near the low end of the range) at mid-reservoir for the
reservoir ecological health index. Hiwassee Reservoir water clarity was the third highest of the tributary
reservoir forcbays, and the highest of all tributary mid-reservoir stations. Secchi depths varied from 2.4 m
at both locations in April, to 5.1 m at mid-reservoir and 5.6 m at the forebay in July.
Sediment Quality—Chemical analyses of sediments in Hiwassee Reservoir in 1993 indicated the
presence of chlordane in the forebay (15 pg/g) and mid-rescrvoir (16 pg/g). Toxicity tests detected acute
toxicity to daphnids in both forebay (15 percent survival) and mid-reservoir (10 percent survival) samples.
Toxicity to rotifers was also detected in the mid-rescrvoir (65 percent survival). Particle size analysis
showed sediments in the forebay were 99 percent silt and clay, and in the mid-reservoir were 90 percent silt
and clay.
Sediment quality ratings used in the overall Hiwassee Reservoir ecological health evaluation for
199.3 were poor at the forebay (due to toxicity to daphnids and presence of chlordane) and poor at the mid-
reservoir site (due to toxicity to daphnids and rotifers and presence of chlordane).
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BenthicMacroinvertebrates—Until 1993, no TVA data on the benthic macroinvertebrate
community in Hiwassee Reservoir existed. Sampling revealed that the forebay and mid-reservoir sites had
poor benthic communities, and the inflow had a fair benthic community. The forebay site had 5 taxa and
127 organisms/m^ and was dominated by Tubificidae (86 percent). The mid-reservoir site had 11 taxa and
2
2,111 organisms/m with Tubificidae as the dominant taxon comprising 86 percent of the total. The
2
Hiwassee inflow had the greatest number of taxa (16) and had 1,605 organisms/m . Tubificidae
(61 percent) was the dominant taxon followed by Procladius sp (21 percent).
The Hiwassee forebay and mid-reservoir benthic samples rated poor due to low diversity, an
absence of EPT and long-lived taxa, and an abundance of tubificids. The inflow fared better than the
previous sites, but still rated only fair.
Fish Assemblage—Shoreline electrofishing (45 transects) and offshore gill netting (36 net-nights)
from the three zones of Hiwassee Reservoir resulted in the collection of 2,958 fish including 27 species.
When green sunfish (39 percent of total catch) were disregarded, the dominant taxa by number in the
remaining sample were blucgill (43 percent), gizzard shad (9 percent), smallmouth bass (8 percent), white
bass (7 percent), and black crappie (6 percent). Electrofishing results indicated total numbers of fish were
approximately the same in the forebay (952) and transition (931) zones with considerably lower numbers in
the inflow (326) zone.
The Reservoir Fish Assemblage Index (RFAI) showed the littoral fish community (based on results
of electrofishing samples) to be poor in all three sample zones of Hiwassee Reservoir (forebay RFAI=28,
transition RFAI=26, and inflow RFAI=28). Gill netting RFAI results rated all three zones good (forebay
RFAI=50, transition RFAI=46, and inflow RFAI=42).
The trophic composition metric group showed maximum scores for both gear types; all other
metric group scores generally reflected the total RFAI score. Combined electrofishing and gill netting RFAI
scores for the forebay (RFAI=39), transition (RFAI=36) and inflow (RFAI=35)zones were rated fair.
Summary of 1993 Conditions - Use Suitability
There were no bacteriological studies conducted on Hiwassee Reservoir in 1993. Although fish
tissue samples were collected in autumn 1993, results were not available at the time this report was
prepared.
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Chatuge Reservoir
Summary of 1993 Conditions - Ecological Health
Water—Hie average flow through Chatuge Reservoir in 1993 was about 88 percent of normal.
The average residence time was 291 days. The reservoir was strongly stratified, with a maximum
temperature difference of 19.1°C in the water column at the forebay in July. The maximum surface
temperature was 29.0°C at the forebay and 28.6°C in Shooting Creek Embavment, both measurements in
July. North Carolina's standard for maximum temperature of Class °C waters is 29°C. At both locations,
low DO (<5.0 mg/1) conditions began developing at the bottom of the water column in July, and depleted
DO (<2.0 mg/1) conditions occurred from August through October. Depleted DO conditions also occurred
in the metalimnion at the forebay in September. The limited extent of the area of DO depletion gave the
forebay a good rating and Shooting Creek Embaymcnt a fair rating in the reservoir ecological health index.
Conductivities were the fourth lowest of the 19 tributary reservoirs, averaging about 25 ^mhos/cm
in April. Conductivities decreased slightly in the photic zone (supersaturated with DO) in the summer and
increased to a maximum of 45 mhos/cm at the bottom of the water column at the forebay in September.
The only time pH exceeded 8.0 was in June and July from the four to eight meter depth. The minimum pH
was 5.8 at the forebay and 5.9 in Shooting Creek Embayment, both in September.
Organic nitrogen concentrations increased from April to August at both locations, 0.04 and
0.23 mg/1 at the forebay and 0.09 and 0.30 mg/1 in Shooting Creek Embaymcnt. Nitrate concentrations
dropped from 0.09 to <0.01 mg/1 at both locations. Total phosphorus concentrations at the two sites tied
for the third lowest concentrations of the 33 tributary reservoir stations. The maximum concentration was
0.004 mg/1 in Shooting Creek Embayment in April. Consequently, TN/TP ratios were very high, ranging
from 47 at the forebay in April to 160 in Shooting Creek Embayment in August. Total organic carbon
concentrations were low, 0.8 and 0.7 mg/1 in April, and 1.5 and 1.8 mg/1 in August at the forebay and
Shooting Creek Embayment. respectively. Chlorophyll a concentrations averaged 2.8 |ig/l at both locations.
This concentration is in the range considered fair in the reservoir ecological health index. Chatuge had the
fourth clearest water of the tributary reservoirs. Secchi depths varied from 2.4 m in August to 4.6 m in July
in Shooting Creek Embayment, and from 3.1 m in April and August to 4.4 m in July at the forebay.
Sediment Quality—Chemical analyses of sediments in 1993 indicated high levels of chromium
(89 mg/kg), copper (56 mg/kg) and nickel (48 mg/kg) in the Shooting Creek forebay area of Chatuge
Reservoir. Toxicity tests detected acute toxicity to daphnids (55 percent survival) in the Hiwassee River
forebay. Toxicity to daphnids (50 percent survival) was also detected in the water column in this forebay.
Reduced survival of daphnids was also detected (60 percent survival) in the Shooting Creek forebay water
column Particle size analysis showed sediments in the forebay were about 75 percent silt and clay,
25 percent sand. In the Shooting Creek forebay sediments were 99 percent silt and clay
Sediment quality ratings used in the overall Chatuge Reservoir ecological health evaluation for
1993 were fair at the Hiwassee River forebay sampling site (toxicity to daphnids in both water and
sediment); and also fair at the Shooting Creek forebay sampling site (presence of chromium, copper, and
nickel and reduced survival of daphnids)
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Benthic Macromvertebrates—The first year that the benthic macroinvertebrate community was
evaluated on Chatuge Reservoir was 1993. Two forebay sites were chosen on Chatuge, and both had good
benthic communities. The first forebay site, at HiRM 122.0, had 1,431 organisms/m representing 22 taxa;
Tubificidae was the dominant taxon comprising 52 percent of the total. The other site, at Shooting Creek
2
mile 1.5, had 23 taxa and 1,065 organisms/m with Tubificidae (37 percent) and the chironomid Zalutschia
zalutschicola (19 percent) as the dominant taxon.
Both forebay sites had excellent diversity and excellent EPT representations, and an average
amount of long-lived organisms in the community. The Shooting Creek site suffered slightly from an above
average density of tubificids, and the HiRM 122 site was slightly impacted from an above average density
of chironomids.
Fish Assemblage—Electrofishing samples (30 transects) in shoreline areas and experimental gill
netting samples (24 net-nights) offshore collected 1,999 individuals with 20 species represented. Bluegill
was the most abundant taxon in Chatuge Reservoir (47 percent of total fish sampled). Redbreast sunfish
(19 percent), spotted bass (7 percent), white bass (5 percent), and gizzard shad (5 percent) followed in
order of density. Note: Three percent of the total sample was comprised of snail bullheads which is the
first documentation of this species in a TVA reservoir. Electrofishing catch rates were much higher in the
forebay zone (78 per 300m transect) than the Shooting Creek arm (32 per 300m transect) However, gill
netting catch rates were similar between the two stations.
The Reservoir Fish Assemblage Index (RFAI) rated both the forebay and Shooting Creek sites fair
for electrofishing (Forebay RFAI=36 and Shooting Creek RFAI=32) and gill netting (forebay RFAI=34
and Shooting Creek RFAI=32) samples. The only metric grouping with consistently high scores was
trophic composition (percent omnivores and insectivores) in the electrofishing sample. Combined
electrofishing and gill netting RFAI's rated both areas fair.
Summary of 1993 Conditions - Use Suitability
There were no bacteriological studies conducted on Chatuge Reservoir in 1993. Although fish
tissue samples were collected in autumn 1993, results were not available at the time this report was
prepared.
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Nottely Reservoir
Summary of 1993 Conditions - Ecological Health
Water—The average flow through Nottely Reservoir in 1993 was about 90 percent of normal, with
an average residence time of 228 days. The reservoir was stratified from April through September, with a
maximum temperature difference in the water column at the forebay of 18.9°C in July. The maximum
surface temperature was 29.3°C at both the forebay and mid-rescrvoir in July. Georgia's standard for
maximum temperature for protection of aquatic life is 30°C. In June, low DO (<5.0 mg/1) conditions began
developing in the forebay bottom waters, while depicted DO (<2.0 mg/I) conditions had already developed
at mid-reservoir. An area of depleted DO developed at the forebay in July, and remained at both locations
through September. The extensive areas of depleted DO gave both locations poor ratings for DO in the
reservoir ecological health index. The vertical mixing of the reservoir in October eliminated areas of low
DO. The area of DO depletion extended to within 7 meters of the surface in July at mid-reservoir.
Conductivities were the fifth lowest of the 19 tributary reservoirs, with an average of about
30 ^mhos/cm in April, decreased slightly in the supersaturated (DO) photic zone in the summer and
increased to a maximum of 49 and 79 (imhos/cm in September at the bottom of the water column at the
forebay and mid-reservoir, respectively. The only time pH exceeded 8.0 was in June and July. The highest
values at the forebay were from the 4 to 7 m depth, and from the 3 to 5 m depth at mid-reservoir. The
maximum pH was 8.8 at both locations The minimum pH was 5.9 in the depths at both locations from
July to September.
Organic nitrogen concentrations were 0 14 mg/1 in April at both locations, and 0.17 and 0.13 mg/1
in August at the forebay and mid-reservoir, respectively. Nitrate-nitrogen concentrations were 0.12 and
0.15 mg/1 in April at the forebay and midreservoir, respectively, dropping in <0 01 mg/1 in August at both
locations. Total phosphorus concentrations at both locations were 0.02 mg/1 in April, dropping to 0.005
and 0.008 mg/1 in August at the forebay mid-reservoir, respectively. Dissolved ortho phosphorus ranged
from a maximum concentration of 0 004 mg/1 in April at mid-reservoir to a minimum of 0.002 mg/1 at both
locations in August. Total organic carbon concentrations varied from a low of 1.2 mg/1 in April to a
maximum of 2.2 mg/1 in August, both at mid-reservoir Chlorophyll a concentrations averaged 3.4 [j.g/1 at
the forebay and 5.0 (ig/1 at mid-rescrvoir. These concentrations are in the range considered good in the
reservoir ecological health index Secchi depths varied from 1.4 m in April at both locations, to 4.2 and
2.4 m in June at the forebay and mid-reservoir, respectively.
Sediment Quality—Chemical analyses of sediments in Nottely Reservoir in 1993 did not reveal
any metal or organic analytes to be of concern Toxicity tests detected acute toxicity to daphnids (70
percent survival) and rotifers (60 percent survival) in the forebay. Particle size analysis showed sediments
in the forebay were 89 percent silt and clay, 11 percent sand; and in the mid-reservoir were about 100
percent silt and clay.
Sediment quality ratings used in the overall Nottely Reservoir ecological health evaluation for 1993
were fair at the forebay sampling site (toxicity to daphnids and rotifers); and excellent at the mid-reservoir
sampling site.
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Benthic Macroinvertebrates—The first year that the benthic macroinvertebratc community' was
evaluated on Nottely Reservoir was 1993. The forebay site, which had a poor benthic community, had 11
2
taxa, 452 organisms/m , and was dominated by Tubificidae (50 percent) and Chironomus sp (29 percent).
The inflow site had a good benthic community. There were more taxa (20) and a greater density (933
2
organisms/m ) than at the forebay site. Tubificidae (34 percent), Chironomus sp (26 percent), and
Procladius sp (23 percent) dominated the benthic community.
A deficiency of EPT taxa and long-lived organisms were the two primary contributing factors for
the poor benthic community at the forebay. Elevated numbers of chironomids and tubificids also
contributed to the poor rating. At the inflow, an opposite scenario surfaced: EPT and long-lived taxa had
an excellent representation, and the tubificid metric was excellent, therefore contributing to a good benthic
community structure.
Fish Assemblage—Only the forebay of Nottely Reservoir was sampled in fall 1992. However, in
1993 a transition zone sample was added to better assess the quality of the fish community. Shoreline
electrofishing (30 transects) in the littoral zone and experimental gill netting (24 net-nights) in the
offshore/deeper areas collected 2,275 individuals with 20 species represented. The four most abundant
species represented in the samples were bluegill (63 percent), black crappie (6 percent), green sunfish
(5 percent), and carp (5 percent). Electrofishing results indicated the primary forage available in Nottely
consisted of sunfish species (69 percent of total catch) instead of shad, as is usually the case.
The Reservoir Fish Assemblage Index (RFA1) rated the littoral fish community (based on results of
electrofishing samples) fair in the transition zone (RFAI=36) and poor in the forebay (RFAI=30) of Nottely
Reservoir. Generally low metric scores in both zones were directly related to low species diversity. Both
areas (transition RFAI=32, and forebay RFAI=34) of Nottely were rated fair by gill netting RFAI analysis.
When electrofishing and gill netting RFAI scores are combined both forebay (RFAI=32) and transition
(RFAI=34) zones rated fair.
Summary of 1993 Conditions - Use Suitability
There were no bacteriological studies conducted on Nottely Reservoir in 1993. Although fish tissue
samples were collected in autumn 1993, results were not available at the time this report was prepared.
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Blue Ridge Reservoir
Summary of 1993 Conditions - Ecological Health
Water—The flow through Blue Ridge Reservoir in 1993 was about normal, with an average
residence time of about 156 days The reservoir was thermally stratified from April through September;
there was no sampling in October The maximum temperature difference in the water column was 17.7°C,
and the maximum surface temperature was 29.8°C, both in July. Georgia's standard for maximum
temperature for protection of aquatic life is 30°C. Low DO (<5.0 mg/I) conditions developed in August; the
lowest DO measured was 3 .4 mg/1 in September. The absence of an area of depleted DO gave Blue Ridge a
good rating for DO in the reservoir ecological health index.
Conductivities averaged about 20 nmhos/cm, the lowest of the 19 tributary reservoirs, and showed
little stratification. The maximum pH was 8.8 at the 7 m depth in July. The minimum pH was 5.6 at the
20 m depth in September.
Organic nitrogen concentrations were 0.04 and 0.08 mg/1 in April and August, respectively.
Nitrate-nitrogen concentrations decreased from 0.06 to <0.01 mg/1 from April to August. Total and
dissolved ortho phosphorus concentrations were 0.003 for both in April, and 0.004 and <0.002 in August.
Total organic carbon concentrations went from 0.7 mg/1 in April to 1.5 mg/1 in August, tied for the second
lowest concentrations in the tributary reservoirs. Chlorophyll a concentrations were the second lowest of
the 33 tributary reservoir stations, averaging 1.8 |Ag/l. This concentration is in the fair range in the reservoir
ecological health index Water clarity was the second highest of the tributary reservoir forebays, with
Secchi depths varying from 3.4 meters in April to 5 4 meters in June.
Sediment Quality—Chemical analyses of sediments in Blue Ridge Reservoir in 1993 did not reveal
any metals or organic analytes to be a concern. Toxicity tests detected acute toxicity to daphnids
(20 percent survival) in the forebay. Particle size analysis showed sediments in the forebay were 95 percent
silt and clay.
Because of the toxicity of the forebay sediment to daphnids, a fair sediment quality rating was used
in the overall 1993 Blue Ridge Reservoir ecological health evaluation.
Benthic Macromvertebrates—The first year that the benthic macroinvertebrate community was
evaluated on Blue Ridge Reservoir was 1993. The forebay, the only sample location, had an excellent
2
benthic fauna, with 1,308 organisms/m representing 23 taxa The dominant taxa were Pisidium sp
(33 percent), Procladius sp (21 percent), Spirosperma nikolskvi (18 percent), and Tubificidae (17 percent).
This site received good scores for five of the six metrics: diversity, number of EPT taxa, number of
chironomids, number of tubificids, and evenness of dominant species. Depressed numbers of long-lived
taxa was the only metric that rated fair.
Fish Assemblage—Only the forebay of Blue Ridge Reservoir was sampled in fall 1993.
Electrofishing samples (15 transects) in shoreline areas and experimental gill netting samples (12 net-
nights) offshore collected 856 individuals with 15 species represented. By far the predominant species
captured was bluegill (59 percent) followed distantly by white bass (10 percent), smallmouth bass
77
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(8 percent), and redbreast sunfish (5 percent). There were three times as many fish collected by
electrofishing as gill netting, largely attributed to high numbers of bluegill inhabiting shoreline areas.
The electrofishing RFAI score of 28 rated poor and gill netting results indicated fair (RFAI=34)
fish community conditions. The combined RFAI scores (RFAI=31) rated the Blue Ridge forebay fair.
Scoring for both electrofishing and gill netting RFAI metrics was influenced by low diversity, low catch,
and dominance by a single species (bluegill).
Summary of 1993 Conditions - Use Suitability
There were no bacteriological studies conducted on Blue Ridge Reservoir in 1993. Although fish
tissue samples were collected in autumn 1993, results were not available at the time this report was
prepared.
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Ocoee Reservoir No. 1 (Parksville Reservoir)
Summary of 1993 Conditions - Ecological Health
Water—The average flow in 1993 was about 91 percent of normal. The high elevation outlet at the
dam allows the hypolimnetic water to remain in place all spring and summer. In October, the bottom
temperature was 7.7°C. The very cold bottom temperatures mean that the reservoir was strongly stratified;
there was a temperature difference in the water column of 21.4°C in July. The maximum surface
temperature was 28.7°C in July. Tennessee's maximum temperature criterion for aquatic life is 30.5°C.
Very little DO depletion occurs in the reservoir; the minimum DO during the survey was 5.8 mg/1 at the
bottom in October. The maximum DO saturation was 108 percent at the surface in May. The lack of low
DO in the reservoir resulted in a good rating for DO in the reservoir ecological health index.
Conductivities were low, usually between 50 and 60 jimhos/cm with little stratification. The lack
of DO depletion and low primary productivity resulted in little variation in pH, which varied from 7.5 to
6.3.
Concentrations of total nitrogen, total phosphorus, total organic carbon, and chlorophyll were all
among the lowest six of the 33 tributary reservoir stations. Organic- and nitrate-nitrogen concentrations
were 0.03 and 0.09 mg/1 in April, and 0.06 and 0.04 mg/1 in August Total and dissolved ortho phosphorus
concentrations were 0.005 and 0.003 mg/1 in April, and 0 002 and <0.002 mg/1 in August. Total organic
carbon concentrations were very low, 0.8 and 1.4 mg/1 in April and August, respectively. Chlorophyll a
concentrations averaged 2.5 ng/1. This chlorophyll concentration is considered fair in the reservoir
ecological health index. Secchi depths varied from 1.6 m in April to 3.6 m in July, September, and October.
Sediment Quality—Chemical analysis of sediments in Parksville Reservoir in 1993 indicated
extremely high levels of copper (1,500 mg/kg), lead (1,300 mg/kg) and zinc (1,500 mg/kg) in the forebay
sediment. Toxicity tests detected acute toxicity to daphnids (0 percent survival) and rotifers (10 percent
survival) at an upper reservoir site sampled only for sediments (not included in the overall ecological health
score). Acute toxicity to daphnids and rotifers was also detected in near bottom water collected at the
forebay (0 and 20 percent survival, respectively); and at the upper reservoir sampling site (0 percent
survival for both species). Particle size analysis showed sediments in the forebay were 99 percent silt and
clay. No chemical analyses or particle size analyses were conducted for the upper reservoir sediment
sample.
Because of the acute toxicity of the forebay bottom water to daphnids and rotifers and the very
high concentrations of copper, lead, and zinc found in the forebay sediment, a poor sediment quality rating
was used in the overall 1993 Parksville Reservoir ecological health evaluation.
Benthic Macroinvertebrates—Only one site was chosen for sampling the first year on Ocoee No.
2
1, located in the forebay. The benthic community there was poor, with only 10 taxa, 372 organisms/m ,
and dominated by Tubificidae (65 percent) and Limnodnlus hoffmeisteri (27 percent). This site rated poor
on 3 of the 5 metrics: number of EPT taxa, number of long-lived taxa, and proportion of tubificids. It
received a good score only on the proportion of chironomids metric, and diversity was fair.
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Fish Community—Only the forebay of Parksville Reservoir was sampled in fall 1993. Shoreline
electrofishing (15 transects) and offshore netting (12 net-nights) produced a total of 524 individuals
including 15 species Bluegill and largemouth bass were the most abundant species collected, comprising
76 and 7 percent of the total sample, respectively. Channel catfish (4 percent) and yellow perch (3 percent)
were also frequently encountered.
The electrofishing Reservoir Fish Assemblage Index (RFAI) rated the Parksville littoral fish
community as poor (RFAI=28) and the gill netting RFAI rated the limnetic bottom fish community as very
poor (RFAI=20).
Overall RFAI analysis (combined electrofishing and gill netting) determined that the quality of the
reservoir fish community was poor. The Parksville Reservoir forebay RFAI of 24 was the lowest recorded
for storage reservoir forebays, receiving minimum scores for seven of the twelve metrics utilized for the
electrofishing RFAI analysis, and ten of the twelve metrics analyzed for gill netting.
Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—No bacteriological studies were conducted in 1993.
Fish Tissue—There are no fish consumption advisories on Parksville Reservoir. However,
screening studies conducted 1987 through 1991 consistently found relatively high PCB concentrations
(about 1.0 (ig/g) and higher than expected selenium concentrations (about 1.0 |ig/g) at the forebay. Because
of the consistently elevated PCB concentrations, TVA, TDEC, and TWRA designed and conducted a more
intensive effort on Parksville Reservoir for autumn 1992. The study included individual analyses on
channel catfish and largemouth bass from the forebay and upper reservoir area and composite analysis of
bluegill sunfish from both areas and rainbow trout from the lower portion of the reservoir. PCBs,
chlordane, selenium, and mercury were the analytes of interest. Results generally fell along expected lines.
PCB concentrations in channel catfish were relatively high (averages 1.5 and 1.0 (ag/g and maxima 3.0 and
1.9 (ig/g at the forebay and upper locations, respectively). PCB concentrations in largemouth bass were not
as high (averages 0.6 and 0.7 jig/g and maxima 1 7 and 2.0 ng/g at the forebay and upper location,
respectively). PCB concentrations in the bluegill and trout composites were only slightly above detection
limits. Chlordane and mercury concentrations were low or not detected in all samples. Selenium
concentrations fell generally as expected (around 1.0 |^g/g). At the time this report was prepared, no action
had been taken on these results. Additional composite samples of channel catfish from the forebay and
inflow areas were collected in autumn 1993, but results were not available at the time this report was
prepared.
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Hiwassee River Stream Monitoring Site
Summary of 1993 Conditions - Ecological Health
Water—The water of the Hiwassee River is soft (average hardness of 15 mg/1) and slightly
alkaline (average total alkalinity of 16 mg/1). The median pH for the stream monitoring site was 7.2. The
river was well oxygenated with dissolved oxygen levels remaining around 100 percent of saturation.
Of the 12 streams monitored across the Tennessee Valley, the Hiwassee River ranked among the
lowest average concentrations of organic nitrogen (0.089 mg/1), nitrate+nitrite-nitrogen (0.16 mg/1), and
total phosphorus (0.025 mg/1). It ranked near the middle in average ammonia nitrogen (0.030 mg/1) and
dissolved orthophosphate (0.007 mg/1) concentrations. The low total phosphorus and nitrate+nitrite-
nitrogen concentrations yielded a good rating for nutrients at the site.
Seven analyses for priority pollutant metals (dissolved cadmium, lead, nickel, silver, and zinc and
total and dissolved copper and zinc) were performed bi-monthly. Dissolved cadmium was detected in 5 of 6
samples One sample exceeded the EPA guidelines for both chronic and acute toxicity to aquatic life.
Another sample exceeded the guideline only for chronic toxicity to aquatic life.
Sediment— Sediment quality rated good in 1993 with no acute toxicity observed. No PCBs or
pesticides exceeded the EPA guidelines; however, nickel exceeded the EPA guidelines. This is an
improvement over 1992 when the sediment quality rated fair.
Benthic Macromvertehrates—In 1993, benthic macroinvertebrate results rated fair with a
1
Modified Benthic Index of Biotic Integrity (MBIBI) score of 38, with 81 taxa and 828 organisms/m .
J
Conditions in 1992 also rated fair (MBIBI score 34) with 65 taxa and 953 organisms/m ; however, the
MBIBI score of 34 was very close to a poor rating. Dominant organisms in 1993 were dipteran midge
larvae (33 percent), caddisflies (18 percent), and mayflies (13 percent). Dipteran midge larvae was the
most dominant organism in 1992 (28 percent), followed by the Asian clam Corbicula (20 percent) and
caddisflies (14 percent). Regulated stream flows and cold water releases from Appalachia Powerhouse
stress warmwater benthic communities in the river.
Fish Community Assessment—No meaningful change was seen in the fish community as ratings
for both 1993 and 1992 were good with Index of Biotic Integrity (IBI) score 48 each year. Limited
deficiencies in number of native species, numbers of darter and sunfish species, proportion of fish as
specialized insectivores, and fish density indicated less than optimum conditions. Problems found in the fish
community may be partially attributed to altered flows due to releases from Apalachia Powerhouse.
Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—No fecal coliform bacteria samples were collected in 1993.
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Fish Tissue—A five-fish composite each of carp, channel catfish, and largemouth was collected
during summer and analyzed for selected metals, pesticides, and PCBs. All analytes were either not
detected or found in low concentrations. The only analyte high enough to be noteworthy was PCBs in carp
with a slightly elevated concentration of 0.6 ^g/g.
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WATTS BAR RESERVOIR, FORT LOUDOUN RESERVOIR,
AND MELTON HILL RESERVOIR WATERSHED
83
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84
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Watts Bar Reservoir
Summary of 1993 Conditions - Ecological Health
Water—During the April-September 1993 monitoring period, surface water temperatures ranged
from a minimum of 18.3°C in April to a maximum of 30.2°C in July in the forebay; and from 16.7°C to
29.8°C (for the same months) at the transition zone. The State of Tennessee's maximum water temperature
criteria for the protection of fish and aquatic life is 30.5°C.
Values for DO at the 1 5m depth ranged from a low of 6.5 mg/1 in September to a high of
12.6 mg/1 in April at the forebay, and from 7.1 mg/1 to 11.3 mg/1 (for the same months) at the transition
zone. At the inflow sampling site on the Tennessee River arm of Watts Bar Reservoir (i.e. the tailrace of
Fort Loudoun dam) a minimum DO of 3.9 mg/1 was recorded in September. At the inflow sampling site on
the Clinch River arm of Watts Bar Reservoir (i.e., the tailrace of Melton Hill dam) a minimum DO of 6.3
mg/1 was recorded in March Tennessee's minimum dissolved oxygen criteria for the protection of fish and
aquatic life is 5.0 mg/1, measured at the 1 5 meter depth
Temperature and dissolved oxygen data show that Watts Bar Reservoir developed a moderate
degree of both thermal and oxygen stratification throughout most of the summer of 1993 For the period
April through August, monthly surface to bottom temperature differentials (AT's) were: 5.2°C, 5.5°C, 7.4°
C, 7.3°C, and 4.0°C at the forebay; and 2.3°C, 2.6°C, 3.9°C, 6.2°C, and 2.2°C at the transition zone.
DO versus depth data show that a rather strong oxycline also developed in Watts Bar Reservoir,
particularly from June through August. During these three months, surface to bottom differences in DO
were: 9 2 mg/1, 9.2 mg/1, and 5 8 mg/1 at the forebay, and 7.2 mg/1, 5.8 mg/1, and 3.1 mg/1 at the transition
zone. At the forebay, near bottom DO concentrations in the hypolimnion were less than 2 mg/1 in June and
July In addition, the proportion of the hypolimnion with low DO's (i.e less than 2 mg/1) averaged about 13
percent of the total cross sectional area, higher than in any other Tennessee River reservoir. The minimum
observed DO concentration in Watts Bar Reservoir in 1993 was 0.6 mg/1 at the bottom of the forebay in
July, but DO's were never less than 4 mg/1 at the transition zone.
DO ratings used in the overall reservoir ecological health evaluation for Watts Bar Reservoir were
poor at the forebay; excellent at the transition zone and at the inflow sampling site on the Clinch River; and
fair at the inflow site on the Tennessee River The low forebay rating was due to the large proportion of the
forebay hypolimnion with low DO concentrations (i.e., less than 2 mg/1). The fair rating at the inflow
sampling site on the Tennessee River arm of Watts Bar Reservoir was a result of oxygen levels being
measured about 1 mg/1, below the Tennessee criteria (5 mg/1, at the 1.5 meter depth) in the releases from
Fort Loudoun dam.
Historically, the pH's of water in Watts Bar Reservoir has been higher than other Tennessee River
sampling site This is due to the addition of the cool, clear, well oxygenated, nitrate rich, and hard water of
the Clinch River which combines with the Tennessee River (and Watts Bar Reservoir) at TRM 567.9,
about seven miles upstream from the transition zone sampling site. In the summer of 1993, values of pH
ranged from 6.8 to 9.0 on Watts Bar Reservoir. During much of the April-September sample period, near
surface values of pH frequently exceeded 8.5 at both the forebay and the transition zone, with DO
saturation values commonly exceeding 100 percent, indicating high rates of photosynthesis. Tennessee's
maximum pH criteria for the protection of fish and aquatic life is 8.5.
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The average total phosphorus concentrations observed in Watts Bar Reservoir (0 029 mg/1 at the
forebay and 0.035 mg/1 at the transition zone) were among the lowest of the Tennessee River Vital Signs
Monitoring locations in 1993. In addition, the average dissolved ortho phosphorus concentrations of
0.007 mg/1 and 0.004 mg/1, respectively, at the forebay and transition zones were also among the lowest
observed at any of the Tennessee River Vital Signs Monitoring locations in 1993. TN/TP ratios on Watts
Bar Reservoir are higher than on any other Tennessee River reservoir. The low phosphorus concentrations
in combination with the relatively high nitrogen concentrations (supplied by both the Clinch and Tennessee
River inflows) results in the high TN/TP ratios in Watts Bar (particularly at the transition zone) and
suggest periods of phosphorus limitation on primary productivity.
The highest chlorophyll a concentrations were measured in August at the forebay (10 |ig/l) and in
May at the transition zone (11 fig/1). Surface concentrations of chlorophyll a averaged about 7 jj.g/1 at the
forebay and about 8 ng/1 at the transition zone in 1993. Consequently, the chlorophyll a ratings used in the
1993 ecological health evaluation for Watts Bar Reservoir were good (i.e., falling in the 3 to 10 fag/1 range)
at both locations.
Forebay Secchi depth and suspended solids measurements averaged 1 5 m and 6.3 mg/1,
respectively. These values indicate the light transparency of Watts Bar Reservoir forebay to be relatively
high compared with other mainstem Tennessee River reservoirs in 1993.
Sediment—Chemical analyses of sediments in Watts Bar Reservoir in 1993 indicated elevated
levels of un-ionized ammonia (240 fj.g/1) in the forebay, and the presence of chlordane (18 fig/kg) in the
transition zone. Mercury was also detected at the transition zone at a slightly elevated level (0.72 mg/kg),
but at a level below sediment quality guidelines for mercury (i.e. 1.0 mg/kg). Toxicity tests detected acute
toxicity to daphnids and rotifers (40 percent survival each) in the forebay. The forebay was also toxic to
rotifers in 1992. Particle size analysis showed sediments from the forebay were near 100 percent silt and
clay; and 98 percent silt and clay from the transition zone.
Sediment quality ratings used in the overall Watts Bar Reservoir ecological health evaluation for
1993 were "poor" at the forebay (acute toxicity to test animals and presence of ammonia); and "good" at
the transition zone (presence of chlordane).
Benthic Macroinvertebrates—The forebay site had a good benthic macroinvertebrate community,
the transition zone fair, and both the Tennessee River and Clinch River inflow sites had poor benthic
communities. The forebay on Watts Bar had 805 organisms/m representing 18 taxa; the dominant species
were the chironomids Chironomus sp (32 percent) and Coelotanvuus tricolor (16 percent). The transition
zone had 14 taxa and 1,280 organisms/2 with the snail Musculium transversum (34 percent), the mayfly
Hexagenia limbata (27 percent) and the chironomid Chironomus sp (17 percent) as the dominant species
present The Tennessee River inflow site had 314 organisms/m representing 20 taxa; Corbicula fluminea
was the dominant species comprising 71 percent of the total organisms The Clinch River inflow site had
2
145 organisms/m made up of 16 taxa; Corbicula fluminea (49 percent), Pseudochironomus sp
(18 percent) and Tubificidae (18 percent), were the dominant taxa.
The Watts Bar forebay scored well on all metrics except for the paucity of EPT taxa and the
preponderance of chironomids. Those two factors kept this site from obtaining an excellent rating. The
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transition zone exhibited a fair community. Reduced diversity, minimal numbers of long-lived species,
above average numbers of chironomids, and unevenness associated with the dominant species all
contributed to the fair rating this site received. The Tennessee River and Clinch River inflow sites both had
a poor benthic communities because of the lack of diversity, EPT taxa, and long-lived species. The
unevenness of dominant taxa also negatively impacted these benthic communities. Interestingly, the percent
of the total organisms comprised of tubificids and chironomids, normally considered tolerant organisms,
was relatively low at both inflows.
Aquatic Macrophytes—Aquatic plants have declined from about 700 acres in the late 1980's to an
estimated 10 acres in 1993. Eurasian watermilfoil and spinyleaf naiad were the dominant species prior to
the recent decline.
Fish Community—Shoreline electrofishing (60 transects) and offshore gill netting (39 net-nights)
sampled a total of 5,174 fish represented by 50 species. Three species made up the majority of the overall
sample: gizzard shad (37 percent), bluegill (13 percent), and emerald shiners (12 percent). Electrofishing
results showed catch rates to be similar in the Clinch River inflow (CPUE=51 per 300m transect),
Tennessee River inflow (CPUE=53 per 300m transect), and forebay (CPUE=56 per 300m transect) but
much higher at the transition zone (CPUE=129 per 300m transect). The higher catch rate in the transition
was attributed mainly to abundance of emerald shiners and bluegill. Threadfin shad YOY catch rates were
moderate in all sample zones except the Tennessee River inflow which was considered high Gill netting
catch rates were much the same in all four sample areas.
The Reservoir Fish Assemblage Index (RFAI) rated the littoral fish community (based on results of
electrofishing samples) good in the transition (RFAI=48), fair in the forebay (RFAI=34) and Tennessee
River inflow (RFAI=34), and poor in the Clinch River inflow (RFAI=30). The lower Clinch River inflow
rating (compared to the Tennessee River inflow) resulted from slightly fewer numbers of sunfish and
intolerant species The gill netting RFAI rated both the transition zone (RFAI=38) and forebay (RFAI=32)
fair Gill netting RFAI values were not calculated for inflow zones of run-of-the-river reservoirs due to low
numbers of replicate samples.
Combined electrofishing and gill netting RFAI scores for the forebay (RFAI=33) received a fair
rating, followed by the transition (RFA1=43) zones which was rated good. Electrofishing RFAI scores for
the Tennessee (RFAI:=34) and Clinch River (RFAI=30) inflow zones were rated fair and poor, respectively
Summary of 1993 Conditions - Use Suitability
Fecal Cohform Bacteria—Fourteen swimming areas were tested for fecal coliform bacteria 12
times each in 1993. Only one sample at each site was collected within 48 hours of a rainfall of at least one-
half inch. Bacteria concentrations were generally higher after rainfall If the one rainfall sample is excluded,
all sites met Tennessee's water quality criteria for geometric mean concentration However, four sites had
one or more concentrations to exceed 1000/100 ml, Tennessee's maximum concentration for one sample
Only three of the fourteen areas had very low geometric mean concentrations for all samples (<20/100 ml),
a much lower ratio than the other Tennessee River Reservoirs. All monthly fecal coliform bacteria samples
taken at the two Vital Signs locations were <10/100 ml.
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Fish Tissue—Fish from Watts Bar Reservoir have been under intensive investigation for several
years because of PCB contamination. TDEC has issued an advisory warning the public to avoid eating
certain species and to limit consumption of other species. Four of these species (channel catfish, striped
bass including striped bass/white bass hybrids, sauger, and white bass) were reexamined in autumn in
1992. Average PCB concentrations among sample sites ranged from 0.4 to 1.9 jig/g for channel catfish
(five sites), 1.0 to 1.1 |ig/g for striped bass (two sites), 0.2 to 0.6 ng/g for sauger (three sites), and the
average for white bass at the single location was 0 7 (ig/g. Additional data for channel catfish and striped
bass collected in autumn 1992 will be available in the future from studies conducted for DOE study. This is
also true for additional fish collected for TVA studies in autumn 1993.
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Fort Loudoun Reservoir
Summary of 1993 Conditions - Ecological Health
Water—Temperature and dissolved oxygen (DO) data show the establishment of stratification
(both a thermocline and oxycline) in Fort Loudoun Reservoir which persisted throughout most of the
summer (April through September) of 1993. Summer surface water temperatures were warmest in July and
coolest in April They ranged from a maximum of 29.3°C to a minimum of 15.8°C at the forebay, and from
30.4°C to 15.5°C at the transition zone. Surface to bottom temperatures differentials (AT's) exceeded 5°C
each month from April through August at the forebay and from May through July at the transition zone.
Maximum thermal stratification occurred in July when AT's were 9.6°C at the forebay, and 10.2°C at the
transition zone.
In Fort Loudoun Reservoir in 1993, DO at the 1 5m depth ranged from a high of 14.5 mg/1 in May
(algal bloom) to a low of 5 4 mg/1 in September at the forebay; and from 12.6 mg/1 to 5.4 mg/1 (for the
same months) at the transition zone. The minimum DO observed in Fort Loudoun Reservoir in 1993 was
2.5 mg/1 at the bottom of the forebay during September. Maximum surface to bottom dissolved oxygen
differentials (DO's) exceeded 5 mg/1 each month, May through August, at the forebay; and, exceeded
4 mg/1 April through June at the transition zone, with a minimum bottom DO of 4.9 mg/1 in September. DO
ratings used in the overall reservoir ecological health evaluation for Fort Loudoun Reservoir were excellent
at both the forebay and the transition zone.
Summer values of pH ranged from 6.9 to 9.4 in Fort Loudoun Reservoir in 1993. At the forebay,
near surface pH values exceeding 8.5 (ranged from 8 8 to 9.3), and DO saturation values exceeding
120 percent (ranged from 121% to 163%) were measured each month from April through August
indicating substantial photosynthetic activity. During May, June, and July, a similar pattern of high pH's
(range 8.6 to 9.4) and high DO saturations (range 132% to 161%) was observed at the transition zone.
Tennessee's maximum pH criteria for the protection of fish and aquatic life is 8.5.
Conductivity ranged from 107 to 221 fimhos/cm, averaging about 185 nmhos/cm at the forebay
and 200 ^mhos/cm at the transition zone. The slightly lower conductivities measured at the forebay were
caused by the mixing of the soft water inflows from the Little Tennessee River, via the Tellico Reservoir
canal with the harder water of the Tennessee River. During the summer, the water in the forebay of Tellico
Reservoir is often cooler (1993 average summer forebay temperature was 16.5C) than the water in the
forebay of Fort Loudoun Reservoir (1993 average summer forebay temperature was 20.6C). During hydro-
electric power generation, water from Tellico Reservoir forebay is pulled into Ft Loudoun forebay and
being cooler (higher density) flows under the warmer water of Fort Loudoun Reservoir. For example, in
Fort Loudoun forebay in September 1993, surface conductivity was approximately 200 (amhos/cm and
near bottom conductivity was about 115 |amhos/cm (i e. lower conductivity because of the addition of
cooler, lower conductivity water from Tellico Reservoir). At the same time, this cooler, epilimnetic water
from Tellico Reservoir has higher DO's than the bottom water in the forebay of Fort Loudoun Reservoir,
resulting in improved hypolimnetic DO's in Fort Loudoun's forebay, and improved DO's in the releases
from Fort Loudoun dam.
Nutrient concentrations (total nitrogen and total phosphorus) have historically (1990-1993) been
high at both the forebay and the transition zone. The average nitrite plus nitrate-nitrogen concentrations of
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0.34 mg/1 (forebay) and 0.43 mg/1 (transition zone); and the average total nitrogen concentrations of
0 .60 mg/1 (forebay) and 0.71 mg/1 (transition zone) were the highest average concentrations of these
nutrients measured in 1993 at any of the Tennessee River Vital Signs Monitoring locations. These high
concentrations of nitrogen are due to a combination of the effect of wastewater discharges in the Knoxville
metropolitan area and the inflows to Fort Loudoun Reservoir from the Holston and French Broad Rivers,
which have relatively high nitrogen concentrations.
The transition zone area of Fort Loudoun Reservoir has historically had lower water clarity than
any of the other Tennessee River Vital Signs sampling sites. In 1993, total suspended solids (TSS)
averaged 13 .4 mg/1, while Secchi depths averaged less than 1 meter. One final interesting piece of data was
the high fecal coliform concentrations, with no antecedent rainfall, measured at both the forebay and
transition zone sampling sites in April (greater than 600 fecal coliform (FC) colonies per 100 ml of water),
which may indicate municipal wastewater treatment interruptions in the Knoxville area. On no other
occasion throughout the summer did fecal coliform concentrations exceed 5 F°C colonies/100 ml.
The highest chlorophyll a concentrations in the forebay occurred in April (24 jj.g/1) and in the
transition zone in May (19 fa.g/1). Surface concentrations of chlorophyll a averaged about 14 .7 (ig/1 and
13.7 (ig/1, at the forebay and transition zone, respectively, among the highest measured at Tennessee River
sampling sites in 1993. The chlorophyll a ratings used in the 1993 ecological health evaluation for Fort
Loudoun Reservoir were fair (i.e., falling in the 10 to 15 (ig/1 range), at both locations; just below the level
considered poor (i.e. greater than 15 fig/1).
Sediment—As 1990-1992, chemical analyses of sediments in 1993 from Fort Loudoun Reservoir
indicated high levels of zinc (300 mg/kg) in both forebay and in transition zone samples. Chlordane was
also detected in sediment at both the forebay (12 (ig/kg) and the transition zone (27 ng/kg). Toxicity tests
detected acute toxicity to daphnids (55 percent survival) in the forebay. Particle size analysis showed
sediments from the forebay and the transition zone were 99 percent silt and clay
Sediment quality ratings used in the overall Fort Loudoun Reservoir ecological health evaluation
for 1993 were poor at the forebay (acute toxicity to test animals and presence of chlordane and zinc); and
good at the transition zone (presence of chlordane and zinc).
Benthic Macrowvertebrates—In 1993, the benthic macroinvertebrate sampling showed fair
communities in the forebay and transition zone, and a very poor community in the inflow. The forebay
benthic community improved and the inflow benthic community declined from 1992. The forebay site on
Fort Loudoun had 1,178 organisms/m representing 15 taxa; Chironomus (45 percent) and Tubificidae
(26 percent) were the dominant organisms. The transition zone had fewer total organisms (987
organisms/m ) but greater taxa richness (22 total taxa) than the forebay site. The transition zone benthic
community this year was more diverse and abundant than the 1992 community. Tubificidae (27 percent)
and the chironomids Chironomus sp (23 percent) and Procladius sp (24 percent) were the most abundant
taxa. The inflow macroinvertebrate community had 747 organisms/m and 18 taxa. Polvpedilum sp
comprised 31 percent of the sample, and Tubificidae and Corbicula fluminea comprised 24 percent of the
total each
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The Fort Loudoun forebay benthic community rating was negatively impacted by the abundance of
chironomids and the lack of EPT taxa. This was balanced by the positive influence of a diverse assemblage
with evenness among the dominant taxa, allowing this site to achieve an overall fair rating. The benthic
community at the transition zone was negatively impacted by the shortage of long-lived taxa and the
abundance of chironomids. This was off-set by the taxa richness and evenness of dominant species
observed at the site, resulting in a fair rating. The inflow site on Fort Loudoun had a very poor benthic
community in 1993 because of low diversity, a shortage of EPT and long-lived taxa, and an overabundance
of the dominant species.
Aquatic Macrophytes—Aquatic plants on Ft Loudoun Reservoir were primarily upstream of
TRM 635. An estimated 25 acres of aquatic plants were present in 1993. Coverage over the past decade
has ranged from 25 to 140 acres, and Eurasian watermilfoil has been the dominant species.
Fish Community—Fish samples from the littoral (45 electrofishing transects) and profundal areas
(34 net-nights) of Fort Loudoun Reservoir produced 3,211 individuals, representing 40 species. The most
abundant taxa was gizzard shad which accounted for 42 percent of the total number collected. Other
abundant species included bluegill (11 percent), yellow bass (10 percent), largemouth bass (9 percent), and
carp (7 percent). Electrofishing results indicated total numbers of fish were approximately the same in the
forebay (907) and transition zones (1,027) Considerably lower numbers in the inflow zone (420) were due
to reduced catch of gizzard shad, bluegill, and largemouth bass. Very high numbers of YOY threadfin shad
were collected by electrofishing in both the transition (CPUE=7,775 per 300m transect) and forebay
(CPUE=7,953 per 300m transect) zones of Fort Loudoun Reservoir. Gill netting catch rate decreased from
37 fish per net night in the forebay to 30 and 6 in the transition and inflow zones, respectively.
The Reservoir Fish Assemblage Index (RFA1) rated the littoral fish community (based on results of
electrofishing samples) very poor in the transition zone (RFAI=14) and poor in the forebay (RFAI=24) and
inflow zones (RFAI=26) The transition RFA1 of 14, which was the lowest score ever observed in TVA
reservoirs, resulted from the lowest possible score for all metrics except percent anomalies. The gill netting
RFA1 rated the transition (RFAI=36) and forebay (RFAI=36) both fair High metric scores were observed
at both areas for percent of tolerant and omnivorous species, and percent anomalies, with low scores for
intolerant and lithophilic spawning species Gill netting RFAI values were not calculated for inflow zones
of run-of-the-nver reservoirs due to low numbers of replicate samples. Combined electrofishing and gill
netting RFAI scores for the forebay (RFAI=30) and transition (RFAI=25) zones and the electrofishing
RFAI for the inflow (RFAI=26) were all rated poor, resulting in the poorest fish community conditions in
TVA run-of-the-river reservoirs.
Summary of 1993 Conditions - Use Suitability
Fecal Cohform Bacteria—One boat ramp was tested for fecal coliform bacteria in 1993. Fecal
coliform concentrations met Tennessee's bacteriological criteria for water contact recreation. The only fecal
coliform bacteria concentrations in the monthly Vital Signs monitoring >10/100 ml were the April samples.
Concentrations were >600/100 ml at both stations.
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Fish Tissue—The sample site for the PCB trend study is near the transition zone at TRM 625. Ten
channel catfish were collected there in autumn 1992. Concentrations in 1992 were higher than had been found in
1990 (average of 1.0 g/g and range of 0.3 to 1.9 g/g) but lower than in 1991 (average of 2.5 g/g and range
1.4 to 4.6 g/g). The 1992 samples had an average of 1.8 g/g and ranged from <0.1 to 4.2 g/g).
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Melton Hill Reservoir
Summary of 1993 Conditions - Ecological Health
Water—In the summer of 1993, thermal stratification began to develop in May and persisted
through September at both the forebay and the transition zone in Melton Hill Reservoir. Temperature
differentials (AT's) exceeding 10°C between the water surface and the bottom were found each month at the
forebay from May through August; and each month at the transition zone from May through July. This
fairly strong thermal stratification of Melton Hill Reservoir is enhanced by the upstream release of cool
water from Norris Dam, which during the summer flows along the bottom of Melton Hill Reservoir.
Surface water temperatures were warmest in July and coolest in April. They ranged from a high of 29.7°C
to a low of 11.5°C at the forebay; and from 28.8°C to 10.9°C at the transition zone. In the late summer the
release of cool water from Norris Dam into the upstream end of Melton Hill Reservoir and the solar
warming as the water moves downstream into the forebay often results in water surface temperatures being
4-5°C cooler at the transition zone than at the forebay In 1993, the average summer water temperatures in
Melton Hill Reservoir (16.7°C at the forebay and 16.5°C at the transition zone) were lower than all other
run-of-the-nver sampling sites except at Tellico Reservoir forebay.
In spite of the thermal stratification, little oxygen stratification and no hypolimnetic anoxia were
found in Melton Hill Reservoir in 1993. Minimum DO's measured in the summer of 1993 were 4.3 mg/1 on
the bottom at the forebay in July; and 6.5 mg/1 on the bottom at the transition zone in September. DO's at
the 1 5m depth in Melton Hill Reservoir in the summer of 1993, ranged from a high of 11 5 mg/1 in May
and June to a low of 9.3 mg/1 in September at the forebay, and from 10.8 mg/1 in April to 7.6 mg/1 in
September at the transition zone Average summer DO's ( = 91 mg/1) and percent oxygen saturation values
( = 92 percent) were higher at the Melton Hill transition zone than any other reservoir Vital Signs sampling
site in 1993. DO ratings used in the overall reservoir ecological health evaluation for Melton Hill Reservoir
were excellent at both the forebay and the transition zone.
The Clinch River flows through the Valley and Ridge physiographic province, a region underlain
by large amounts of limestone and dolomite. Consequently, Melton Hill Reservoir has relatively high pH
and conductance; in fact, the highest among the run-of-the-river reservoirs. In the summer of 1993, pH
ranged from 7 .3 to 8.8 and conductivity ranged from 223 to 272 ^mhos/cm and averaged about
255 ^mhos/cm in Melton Hill Reservoir. At the forebay, near surface water pH's exceeded 8.5 each month
from May through August, coincident with DO super-saturation values (>110%), and indicative of
photosynthetic activity. Tennessee's maximum pH criteria for the protection of fish and aquatic life is 8.5.
Average nitrite plus nitrate-nitrogen concentrations were quite high in Melton Hill Reservoir. As in
past years, the 1993 average concentration at the transition zone (0.56 mg/1) was the highest nitrite plus
nitrate-nitrogen among all Vital Signs locations sampled.
Dissolved ortho phosphorus concentrations (the only form of phosphorus assimilated by algal cells)
averaged only about 0.003-0.004 mg/1 at the forebay and transition zone, respectively, among the lowest
measured at run-of-the-river sampling sites in 1993. Further. TN/TP ratios were often high (>50)
indicating frequent episodes of phosphorus limitation to algal productivity in Melton Hill Reservoir.
Consequently, average summer chlorophyll a concentrations of 5.3 (ag/1 at the forebay and 4 jj.g/1 at the
transition zone, may reflect a limiting nutrient effect. The highest chlorophyll a concentrations measured
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were 6-7 ng/1 at both the transition zone and the forebay. The chlorophyll a ratings used in the 1993
ecological health evaluation for Melton Hill Reservoir were "good" (i.e., falling in the 3 to 10 jig/l range),
at both locations; just above the level considered fair (i.e., less than 3 |ig/l).
The water clarity (Secchi depth, suspended solids, color, etc.) of Melton Hill Reservoir was
comparatively high and measurements were generally stable throughout the year, being largely influenced
by discharges from Norris Dam rather than localized rainfall runoff events.
Sediment—Chemical analyses of sediments in Melton Hill Reservoir in 1993 indicated the
presence of chlordane in one of two forebay samples (25 ng/kg) and also in the transition zone (32 ng/kg)
sample. Toxicity tests detected no acute toxicity to the two organisms tested. Particle size analysis showed
sediment in the forebay were 99 percent silt and clay and from the transition zone were 90 percent silt and
clay.
Sediment quality ratings used in the overall Melton Hill Reservoir ecological health evaluation for
1993 were "good" at both the forebay and the transition zone (presence of chlordane).
Benthic Macroinvertebrates—The 1993 benthic communities at all three sites on Melton Hill
declined from 1992. The forebay and inflow had a poor benthic macroinvertebrate community and the
transition zone had a very poor benthic community. Melton Hill forebay had 16 taxa and 363
2
organisms/m , a decrease in both diversity and dominance from 1992. The benthic community was
dominated by Chironomus sp (49 percent) and Tubificidae 17 percent. The transition zone had 362
2
organisms/m representing 21 taxa, predominately Tubificidae (36 percent) and Chironomus (27 percent).
2
The inflow location had the greatest abundance (1,649 organisms/m ) and diversity (29 taxa) of all
locations sampled on Melton Hill There was a substantial increase in diversity and density in the inflow
compared to the previous year. Tubificidae (49 percent) and Paratendipes (17 percent) were the dominant
organisms at this site.
Several factors contributed to the poor benthic communities found on Melton Hill Reservoir. Three
factors that negatively impacted all three locations were a preponderance of chironomids, and low numbers
of EPT and long-lived taxa. The problems were further compounded at the transition and inflow sites
because of decreased diversity and inflated numbers of tubificids.
Aquatic Macrophytes—An estimated 240 acres of aquatic macrophytes occurred on Melton Hill
Reservoir in 1993. Eurasian watermilfoil was the dominant aquatic plant and was most abundant from
CRM 24 to 51. Coverage over the past decade has generally ranged from about 100 to 250 acres.
Fish Community—Electrofishing (45 transects) and gill netting efforts (34 net-nights) on Melton
Hill Reservoir produced a total of 2,437 fish representing 42 species. Gizzard shad was the most numerous
species (56 percent of the total number of fish sampled), followed in abundance by yellow bass (8 percent), _
largcmouth bass (5 percent), carp (5 percent), and bluegill (4 percent). The threadfin shad YOY catch rate
(CPUE=335 per 300m electrofishing transect) was moderate in the forebay zone of Melton Hill Reservoir
and insignificant in the transition and inflow areas. Overall fish abundance was much the same in the
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forebay (1,172) and transition (1,108) zones but substantially less in the inflow (157). Fewer species were
also collected from the inflow zone (16) than the forebay (28) or transition zone (36).
The Reservoir Fish Assemblage Index (RFAI) rated the littoral fish community (based on results of
electrofishing samples) fair in the transition (RFA1=32), poor in the inflow (RFA1=22), and very poor in
the forebay (RFAI=18) zones of Melton Hill Reservoir. The very poor rating in the forebay, which
represented the lowest RFAI score for all run-of-the-river forebays, resulted from minimum scores for all
metrics except number of sucker and intolerant species. The gill netting RFAI rated both the forebay
(RFAI=38) and transition (RFAI=40) zones fair. The only extreme difference between the two zones in
metric scoring resulted from higher numbers of lithophilic spawning species in the transition. Gill netting
RFAI values were not calculated for inflow zones of run-of-the-river reservoirs due to low numbers of
replicate samples.
Combined electrofishing and gill netting RFAI scores rated the transition zone (RFAI=36) fair. The
poor RFAl's of 28 and 22 in the forebay and inflow zones, respectively, were the lowest recorded for
comparable zones of run-of-the-river reservoirs in 1993 (Note: Results from biomonitoring on Melton Hill
Reservoir like Tellico, were compared to results from mainstream reservoirs due to similar operational
characteristics. These reservoirs lack deep drawdown which occurs in storage impoundments and have a
navigation lock.)
Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—No bacteriological studies were conducted at recreation areas in 1993.
The April fecal coliform bacteria concentrations at the Vital Signs locations were 113 and 191/100 ml at
the forebay and transition zone, respectively. All other concentrations were <20/100 ml.
Fish Tissue—PCB contamination in catfish from Melton Hill Reservoir has been under study for
several years. Because of this contamination, the TDEC has advised the public not to eat these catfish.
TVA participates on a study team with TDEC, TWRA, and ORNL to investigate PCBs and other
contaminants in fish from east Tennessee Reservoirs. In 1992 ORNL collected and analyzed channel
catfish from the forebay, while channel catfish from near the transition zone and inflow were collected and
analyzed by TVA. Average PCB concentrations from these same locations were 0.8, 1.0, and 0.5 (ig/g,
respectively, and average chlordane concentrations were 0.07, 0.10, and 0.05 jj.g/g, respectively.
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Emory River Stream Monitoring Site
Summary of 1993 Conditions - Ecological Health
Water—The water of the Emory River is soft (average hardness of 24 mg/1) and slightly alkaline
(average total alkalinity of 16 mg/1). The median pH for the stream monitoring site was 7.5. The river was
well oxygenated with dissolved oxygen levels ranging from 88 to 102 percent of saturation.
Of the 12 stations monitored in the Tennessee Valley, the Emory River had the lowest
concentrations of nitrate+nitrite-nitrogen (0.10 mg/1), total phosphorus (0.020 mg/1), and dissolved
orthophosphate (0.002 mg/1). The low organic nitrogen (0.195 mg/1) and ammonia nitrogen (0.002 mg/1)
concentrations were in the lower third of all stations. The good total phosphorus and nitrate+nitrite-nitrogen
concentrations, in particular, contributed to a good nutrient rating for the station.
Seven analyses for priority pollutant metals (dissolved cadmium, lead, nickel, silver, and zinc and
total copper and zinc) were performed bi-monthly. Dissolved cadmium (5 of 6 samples), dissolved nickel (2
of 6 samples) and zinc were detected. All were within EPA guidelines for the protection of aquatic life and
human health.
Sediment—Sediment quality rated good in 1993 with no acute toxicity observed and no metals,
PCBs, or pesticides exceeding the EPA guidelines. This is a significant improvement over 1992 when
sediment quality rated poor
Benthic Macroinvertebrates—In 1993, benthic macroinvertebrate community rated fair with a
1
Modified Benthic Index of Biotic Integrity (MB1BI) score of 39, with 102 taxa and 4,308 organisms/m .
Conditions in 1992 also rated fair (MBIBI score 38) with 77 taxa and 3,137 organisms/m . Benthic
organisms have essentially remained unchanged between sampling years with the exception of a 25 percent
increase in total taxa reported in the qualitative sample. Dominant organisms in 1993 were dipteran midge
larvae (62 percent), coleopteran riffle beetles (13 percent), and caddisflies (10 percent) Dipteran midge
larvae was also the most dominant organism in 1992 (56 percent), followed by caddisflies (14 percent) and
mayflies (12 percent) Siltation from coal mining practices in the Emory River watershed are a continuing
problem for benthic organisms at this site.
Fish Community Assessment—The fish community rated good with an Index of Biotic Integrity
(IBI) score of 52, improving from the borderline good (IBI = 46) rated in 1992. The 1993 fish sample
contained no hybrids and fewer diseased fish, and had a slightly increased fish density suggesting less
stressful conditions for fish since 1992. Minor problems, however, continued to be seen in species
composition and trophic structure A contributing factor of stress on fish at this station is naturally-
occurring low flow (usually less than 50 cfs) during mid to late summer. Low flow reduces fish habitat,
reduces the river's ability to assimilate pollutants, and generally makes the aquatic fauna more vulnerable to
environmental degradation.
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Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—There were no bacteriological studies conducted on the Emory River in
1993.
Fish Tissue—A five fish composite each of carp, channel catfish, and largemouth were collected
during summer 1992 and analyzed for selected metals, pesticides, and PCBs. Mercury was detected in all
three samples but at concentrations which would not be considered elevated. Chlordane was detected at low
concentrations in two samples, and PCBs were found in all samples (carp 0.4 (ig/g; channel catfish
1.2 ng/g; and largemouth bass 0.6 (ig/g). Additional catfish and largemouth bass were collected in summer
1993, but results were not available at the time this report was prepared.
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CLINCH RIVER AND POWELL RIVER WATERSHED
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Norris Reservoir
Summary of 1993 Conditions - Ecological Health
Water—Surface water temperature ranged, for the months it was measured (April-October), from
12.6°C in April to 29.8°C in July in the forebay, from 14.9°C to 30.0°C for the same months at the Clinch
mid-reservoir sampling location, and from 14.6°C to 30 1°C for the same months at the Powell mid-
reservoir sampling location. Thermal stratification was evident in Norris Reservoir in 1993. While this
stratification was evident in April, when the first measurements for the year were made, it became much
stronger beginning in May, due to drastically decreased streamflow combined with solar heating. Maximum
surface to bottom water column temperature differentials occurred in July, when the surface temperatures
were about 22°C warmer than bottom temperatures in the forebay, and about 19°C at the mid-reservoir
sampling locations. The strong thermal stratification in Norris Reservoir persisted through October for the
forebay, and through September for the mid-reservoir locations.
Dissolved oxygen at the 1.5m depth ranged from 9.7 mg/1 in May to 7.4 mg/1 in September at the
forebay, from 10.8 mg/1 in April to 7.0 mg/1 in August at the Clinch mid-reservoir sampling location, and
from 10.2 mg/1 in May to 6.7 mg/1 in October at the Powell mid-reservoir sampling location. During the
summer of 1993, (as in past summers) anoxic conditions developed at all three sampling locations on
Norris Reservoir At the mid-reservoir sampling locations, dissolved oxygen concentrations near the bottom
were approximately 0 mg/1 in July, August, and September. Further, in August this anoxia development
resulted in hypolimnctic dissolved oxygen concentrations being less than 1 mg/1 over approximately two-
thirds of the water column depths in the mid-reservoir sampling locations. For the forebay, anoxic
conditions existed at the bottom in September and October.
DO ratings used in the overall reservoir ecological health evaluation for Norris Reservoir were
poor at the forebay and very poor at the mid-reservoir sampling locations. The forebay DO rating was poor
because approximately 10 percent of the cross-sectional area (six-month summertime average) of the
forebay had a dissolved oxygen concentration less than 2.0 mg/1; anoxic bottom conditions existed; and,
over 20% of this site's cross-sectional bottom length (six-month summertime average) had a dissolved
oxygen concentration less than 2.0 mg/1. The mid-reservoir sites both received very poor ratings for
dissolved oxygen because of even poorer DO conditions. At both sites over 20 percent of the cross-
sectional areas (six-month summertime average) had a dissolved oxygen concentration less than 2.0 mg/1;
both had anoxic bottom conditions; and both had over 50 percent of each site's cross-sectional bottom
length (six-month summertime average) with dissolved oxygen concentrations less than 2.0 mg/1.
In 1993, values of pH in Norris Reservoir ranged from 7.0 to 8.7 for the three monitoring
locations Surface water pH values slightly exceeded 8.5 (Tennessee's maximum pH criteria for the
protection of fish and aquatic life is 8.5) at the forebay in August, at the Clinch mid-reservoir location in
June, and at the Powell mid-reservoir location in May and June. In each of these cases, dissolved oxygen
saturation concentrations were high (>100 percent), which indicates substantial photosynthetic activity.
The conductivity of the water in Norris Reservoir is among the highest of all the reservoirs in the Tennessee
River drainage. Reservoir-wide, conductivities ranged from 172 to 382 ^mhos/cm. They averaged
244 nmhos/cm at the forebay, 277 ^mhos/cm at the Clinch mid-reservoir sampling location, and
295 ^mhos/cm at the Powell mid-reservoir sampling location.
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Concentrations of nutrients were very low, which is typical for Norris Reservoir. Average total
phosphorus (TP) and dissolved ortho phosphorus (DOP) were especially low reservoir-wide At the
forebay, both TP and DOP averaged less than 0.002 mg/1 and were among the lowest average total
phosphorus concentrations measured in 1993. Further, TN/TP ratios for individual samples often exceeded
100 at all Norris sampling sites, which indicates extremely limiting phosphorus conditions on algal
productivity in the reservoir.
Concentrations of chlorophyll a averaged only 1.7 (ig/1 at the forebay, 4.1 jj.g/1 at the Clinch mid-
reservoir sampling location, and 3.6 fig/1 at the Powell location. The chlorophyll a ratings used in the 1993
ecological health evaluation for Norris Reservoir were fair at the forebay (i.e. less than 3 fig/1) and good
(i.e. falling in the 3 to 10 (j.g/1 range), at both mid-reservoir locations; just above the level considered fair
(i.e. less than 3 fxg/1).
The water of Norris Reservoir, especially in the forebay area has historically been quite clear.
However, Norris Reservoir forebay in 1993 was less clear than 1992 with an average Secchi depth of 2.5
meters. The Clinch mid-reservoir Secchi depth was slightly clearer than in 1992, averaging 2.5 meters, and
the Powell was about the same, averaging 2.2 meters.
Sediment—As in 1990-92, chemical analyses of sediments in Norris Reservoir in 1993 found high
levels of lead (76 mg/kg) in the forebay, and elevated levels of un-ionized ammonia in both the Clinch
(375 (ig/1) and Powell (370 (J.g/1) mid-reservoir regions. Toxicity tests detected no acute toxicity to the two
organisms tested. Particle size analysis showed sediments from the forebay were about 100 percent silt and
clay; from the Clinch mid-reservoir were about 95 percent silt and clay; and from the Powell mid-reservoir
were 98 percent silt and clay.
Sediment quality ratings used in the overall Norris Reservoir ecological health evaluation for 1993
were good at the forebay (presence of lead); and good at both of the mid-reservoir sites (presence of
ammonia).
Benthic Macromvertebrates—Among the three reservoir monitoring locations on Norris
Reservoir, the Powell River mid-reservoir site had the highest number of benthic taxa (23) and greatest
density (1,887 organisms/m ), and received the best overall benthic rating of good. The dominant taxa were
Tubificidae (39 percent), Limnodrilus sp (21 percent) and Chironomus sp (22 percent). The forebay and
Clinch River mid-reservoir site both had fair benthic communities. The forebay site had 16 taxa and 751
2
organisms/m ; Tubificidae, the dominant taxon, comprised 56 percent of the total, followed by Corbicula
2
fluminea (26 percent). The Clinch River mid-reservoir location had 1,214 organisms/m representing 17
taxa and was dominated by Tubificidae (52 percent) and Chironomus sp (36 percent).
The Norris forebay could have achieved a good rating had it not been for the abundance of
tubificids and the dearth of EPT taxa These negative influences were offset by the abundance of long-lived
taxa and low numbers of chironomids. The Powell River site, which received a good rating, scored well
because of its diversity and evenness of the dominant taxa. All other metrics evaluated were fair. The
Clinch River site had an average benthic community primarily because all metrics evaluated received only a
fair score. The only metric that rated very low was the dominance metric; in this instance, Tubificidae
comprised an overwhelmingly large percentage of the total organisms collected.
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Fish Assemblage—The fish samples from the littoral (45 electrofishing transects) and profundal
areas (36 net-nights) of Norris Reservoir produced a total of 1,602 individuals representing 29 species.
Highest concentrations of fish were found in the Clinch River transition zone (43 percent of total fish
sampled) due to the abundance of walleye in the gill netting sample (10 per net night) and black basses
(smallmouth, spotted, and largemouth) in the electrofishing sample (9 per 300m transect). The forcbay
electrofishing catch rate (CPUE=15 per 300m transect) was the lowest recorded among all tributary
reservoir forebays The forebay gill netting catch rate (CPUE=7 per net night) was the second lowest
recorded (Parksville forcbay was the lowest). Twenty-five species were collected at both transition zones
and 16 in the forcbay.
The Reservoir Fish Assemblage Index (RFA1) rated the littoral fish community (based on results of
electrofishing samples) good in the Powell River transition (RFAI=46) zone and fair in both the Clinch
River transition (RFAI=40) and forebay (RFA1=34) zones The higher RFA1 in the Powell River transition
zone was influenced by maximum metric scores for diversity, number of piscivorc, sucker, intolerant, and
lithophilic spawning species, percent tolerant species and dominance by a single species. Both the Powell
and Clinch rivers received gill netting RFAI values of 50 classifying them good. The forebay (RFAI=28)
was poor; only one metric (percent anomalies) had a maximum score in the forcbay of Norris; all other
scores were either minimum or midrange Combined electrofishing and gill netting RFAI scores for both the
Clinch (RFAI=45) and Powell (RFAI=48) river transitions were rated good, followed by a fair rating in the
forebay (RFA1=31).
Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—Two swimming beaches, one boat ramp, and one site upstream and
another downstream of the Jacksboro sewage treatment plant were tested for fecal coliform bacteria twelve
times each in 1993 Two samples at each site were collected within 48-hours of rainfall of at least one-half
inch. Bacteria concentrations at all five sites were very low (geometric mean <20/100 ml)
Fish Tissue—Fish tissue samples for screening studies were collected on Norris Reservoir in
autumn 1992. All analytes were low except for PCBs, which were highest at the forebay where the
concentration was 0.9 jag/g. Concentrations at the other two locations were low. Screening samples were
collected again in autumn 1993 to further evaluate PCB concentrations but results were not available at the
time this report was prepared.
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Clinch River Stream Monitoring Site
Summary of 1993 Conditions - Ecological Health
Water—The water of the Clinch River is moderately hard (average hardness of 147 mg/1) and
alkaline (average total alkalinity of 120 mg/1) The median pH for the stream monitoring site was 8.0 The
river was well oxygenated with dissolved oxygen levels ranging from 81 to 106 percent of saturation.
Of the 12 streams monitored across the Tennessee Valley, the Clinch River ranked among the
lowest in average concentrations of ammonia nitrogen (0.015 mg/1) and dissolved orthophosphate
(0.003 mg/1). It ranked just below the median in average concentrations of organic nitrogen (0.198 mg/1),
nitrate+nitrite-nitrogen (0.30 mg/1), and total phosphorus (0.020 mg/1). The low concentrations of total
phosphorus and nitrate+nitrite-nitrogen yielded a good nutrients rating for the station
Seven analyses for priority pollutant metals (dissolved cadmium, lead, nickel, silver, and zinc and
total copper and zinc) were performed bi-monthly Dissolved cadmium was detected in 4 of 6 samples, but
did not exceed the EPA guidelines for the protection of aquatic life and human health
Sediment—Sediment quality rated good in 1993 with no acute toxicity observed and no metals,
PCBs, or pesticides exceeding the EPA guidelines. This is an improvement over 1992 when sediment
quality rated fair.
Benthic Macroinvertebrates—In 1993, bcnthic macroinvertebrate results rated good with a
Modified Benthic Index of Biotic Integrity (MBIBI) score of 53, with 83 taxa and 2,726 organisms/m
Conditions in 1992 also rated good (MBIBI score 50) with 85 taxa and 3,326 organisms/m . The Clinch
River is rated the best among the 12 stream monitoring sites. The benthic fauna in 1993 was composed
mostly of river snails (33 percent), nutrient tolerant oligochaeta worms (16 percent), and mayflies
(14 percent). Mayflies were the dominant organism in 1992 (46 percent), followed by river snails
(13 percent) and coleopteran riffle beetles (9 percent). Overall, conditions remain unchanged between
sampling years
Fish Community Assessment—The fish community rated good with an Index of Biotic Integrity
(IB1) of 50 in 1993, showing no change since 1992 Minor problems were seen in species composition,
trophic structure, and fish condition The fish assemblage was basically intact with a good number of
native species and a healthy compliment of darter, sucker, and intolerant species. Trophic structure was
good at the lower levels, as most fish found were specialized insectivores. Fish density was also at a normal
level. Detrimental conditions observed at this station included occasional bank erosion and siltation
Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—The weir downstream of Norris Dam and the canoe launch site
downstream of the weir were tested for fecal coliform bacteria twelve times each in 1993. Two samples
were collected within 48 hours of rainfall of at least one-half inch. The geometric mean of fecal coliform
bacteria concentrations were very low (<20/100 ml)at both sites.
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Fish Tissue—A five fish composite each of carp, channel catfish, and largemouth bass were
collected during summer 1992 and analyzed for selected metals, pesticides, and PCBs. All analytes were
not detected or found in low concentrations.
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Powell River Stream Monitoring Site
Summary of 1993 Conditions - Ecological Health
Water—The water of the Powell River is moderately hard to hard (average hardness of 150 mg/I)
and alkaline (average total alkalinity of 125 mg/1). The median pH for the stream monitoring site was 8.0.
The river was well oxygenated with dissolved oxygen levels ranging from 88 to 105 percent of saturation
Of the 12 streams monitored across the Tennessee Valley, the Powell River ranked in the lower
half in concentrations of nutrients The average ammonia nitrogen concentration (0.013 mg/1) was the
lowest for the network. The good average total phosphorus (0.035 mg/1) and nitrate+nitrite-nitrogen
(0.47 mg/1), in particular, yielded a good rating for nutrients at the site.
Seven analyses for priority pollutant metals (dissolved cadmium, lead, nickel, silver, and zinc and
total copper and zinc) were performed bi-monthly. Dissolved cadmium (5 of 6 samples) and dissolved
nickel (1 of 6 samples) were detected. Neither metal exceeded the EPA guidelines for the protection of
aquatic life or human health Additional metals analyses included total and dissolved forms of iron and
manganese. Total iron exceeded the EPA guideline for combined consumption of fish and water in one
sample. Total manganese was detected in 4 of 6 samples, but none exceeded EPA guidelines.
Sediment—Sediment quality rated good in 1993 with no acute toxicity observed and no metals,
PCBs, or pesticides exceeding the EPA guidelines. This is a significant improvement over 1992 when
sediment quality rated poor.
BenthicMacrowvertebrates—In 1993, the benthic macroinvcrtcbrate community rated good with
2
a Modified Benthic Index of Biotic Integrity (MBIBI) score of 47, with 94 taxa and 2,586 organisms/m
2
Conditions in 1992 rated fair (MBIBI score 42) with 66 taxa and 2,167 organisms/m . Dominant
organisms in 1993 were dipteran midge larvae (27 percent), river snails (24 percent), and coleopteran riffle
beetles (16 percent) River snails were the most dominant group in 1992 (43 percent), followed by dipteran
midge larvae (24 percent) and the Asian clam Corbicula (10 percent) Overall, conditions improved from
fair to good over the previous year
Fish Community Assessment—Meaningful improvement was seen in the fish community in 1993.
Ratings of good were found for both 1993 and 1992, however the Index of Biotic Integrity (IBI), on which
the ratings are based, increased from 48 in 1992 to 56 in 1993 and was approaching an excellent rating.
Improvement was seen in species richness and composition, trophic structure, and fish density. Only slight
deficiencies in number of darter species and proportion of piscivorous fish prevented a higher rating.
Accumulations of sand, coal, and gravel were observed in some pool areas, but apparently were not a
major problem for the fish community.
Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—No fecal coliform bacteria samples were collected and analyzed above
the stream monitoring site
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Fish Tissue—A five fish composite each of freshwater drum, channel catfish, and largemouth bass
were collected during summer 1992 and analyzed for selected metals, pesticides, and PCBs. All analytes
were not detected or found in low concentrations.
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LITTLE TENNESSEE RIVER WATERSHED
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Tellico Reservoir
Summary of 1993 Conditions - Ecological Health
Water—Fairly strong thermal stratification persisted from April through September 1993 at both
the forebay and transition zone. From June through August, temperature differentials between the water
surface and bottom equaled or exceeded 11°C at the forebay and 10°C at the transition zone. These
differentials were due to a combination of atmospheric warming of surface water—intensified by the low
strcamflows in April and May and the intrusion of surface waters from Fort Loudoun forebay—contrasted
with the inflow of cool bottom water from the releases of Chilhowee Dam upstream. Surface water
temperatures ranged from lows in April to highs in July (i.e. from 16.1°C to 28.0°C at the forebay and
from 16.3°C to 29.5°C at the transition zone). Water in Tellico Reservoir was relatively cool, particularly
at the transition zone which was influenced by the releases from Chilhowee Dam. Summer temperatures
averaged 16.5°C and 17.5°C at the forebay and transition zone, respectively, among the lowest
temperatures for run-of-the-rivcr Vital Signs sampling sites in 1993.
DO at the 1.5m depth ranged from a high of 11.4 mg/1 in April to a low of 6.8 mg/1 in September
at the forebay; and from 10.6 mg/1 to 8.1 mg/1 (for the same months) at the transition zone. From June
through September a persistent oxycline was present in the forebay. Differences between surface and
bottom DO concentrations were 5 to 9 mg/1, and near bottom concentrations were less than 1 mg/1 in
August and September This near bottom, cool, low DO water was very low in conductivity
(<50 ^mhos/cm). This suggests that cool water, which is fairly high in DO when it is released from
Chilhowee Dam, becomes trapped in the hypolimnion of Tellico Reservoir and is slowly depleted of oxygen
content during the summer. The minimum DO was 4.1 mg/1 in July, on the bottom at the transition zone
DO ratings used in the overall reservoir ecological health evaluation for Tellico Reservoir were fair at the
forebay (due to the hypolimnetic anoxia in August and September) and excellent at the transition zone
The Little Tennessee Rjver drains through the Blue Ridge physiographic province—a
mountainous, largely forested region underlain, for the most part, by crystalline rocks The upper slopes of
the watershed have generally thin soils and weathered rock. In addition, the underlying rocks, broadly
speaking arc siliceous and not easily dissolved Surface drainage is rapid, and consequently, the water of
the Little Tennessee River (and Tellico Reservoir) are quite soft, low in pH and conductivity, and low in
nutrients.
In 1993, Tellico Reservoir pH values ranged from 6.0 to 8.9. Near surface pH's exceeded 8.5 at
the forebay in June and July and at the transition zone in July, coincident with DO super-saturation values
indicative of photosynthetic activity. Values of pH in Tellico Reservoir were the lowest of any of the run-
of-the-rivcr Vital Signs reservoirs, averaging 7.0 at both the forebay and transition zone. Values of pH
below the Tennessee minimum criterion of 6 5 for fish and aquatic life were observed in the hypolimnion of
Tellico Reservoir at both the forebay and transition zone in 1993.
The conductivity of water in Tellico Reservoir was also quite low, averaging about 35 (imhos/cm
at the transition zone and 65 ^mhos/cm at the forebay. Mixing of forebay surface waters between Fort
Loudoun and Tellico reservoirs via the inter-reservoir canal influences water quality and causes the higher
measured conductivity at Tellico forebay compared with Tellico transition zone
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Total nitrogen concentrations were low and averaged only 0.33 mg/1 at the forebay and 0.22 mg/1
at the transition zone. Dissolved ortho phosphorus concentrations (the only form of phosphorus assimilated
by algal cells) were also quite low, averaging only 0.003 mg/1 at the forebay and transition zone. Together,
these nutrient concentrations were among the lowest measured concentrations at Vital Signs Monitoring
locations in 1993; and consequently, primary productivity could be expected to be limited much of the time.
Average summer chlorophyll a concentrations were 7 ju.g/1 at the forebay and 3 (ig/1 at the
transition zone. The highest single sample chlorophyll a concentrations measured in 1993 were 9 (ag/1 at the
forebay and only 6 ng/1 at the transition zone. The chlorophyll a ratings used in the 1993 ecological health
evaluation for Tellico Reservoir were good (i.e. falling in the 3 to 10 \xg!\ range), at both locations; just
above the level considered fair (i.e. less than 3 (ig/1).
Water clarity data (as measured by Secchi depth, suspended solids, color, etc.) was comparatively
high with little relative variation throughout the year. This is because inflows to Tellico Reservoir are
primarily a result of Chilhowee Dam discharges which are of high clarity and low color, rather than rainfall
runoff events.
Sediment—Samples for toxicity testing and chemical analyses were collected at three sites in
Tellico Reservoir in 1993: the forebay (LTRM 1.0); and two transition zone locations (LTRM 15.0,
downstream of the confluence of the Tellico River, and LTRM 21.0, upstream of the confluence of the
Tellico River). Chemical analyses of sediments in Tellico Reservoir in 1993 indicated the presence of
chlordane in the forebay (21 ng/kg) and in one of two transition zone (LTRM 15.0) samples (16 (ig/kg).
Toxicity tests detected acute toxicity to daphnids (0 percent survival) at all sampling sites tested; however,
for the first time since 1990, toxicity to rotifers was not detected. Particle size analysis showed sediments
from the forebay were about 97 percent silt and clay; from LTRM 15.0 transition zone were 91 percent silt
and clay; and from LTRM 21.0 transition zone were about 66 percent silt and clay, 34 percent sand.
Sediment quality ratings used in the overall Tellico Reservoir ecological health evaluation for 1993
were poor at the forebay (acute toxicity to test animals and presence of chlordane); poor at the transition
zone site-LTRM 15 .0 (acute toxicity to test animals and presence of chlordane). Information from the
transition zone site at LTRM 21.0 was not included in the overall ecological health rating.
Benthic Macroinvertebrates—The benthic community in Tellico Reservoir in 1993 rated poor at
both the forebay and transition zone. The forebay zone had 17 taxa and 433 organisms/m dominated by
Tubificidae (65 percent of the total), which is very similar to the benthic community observed the previous
2
year. The transition zone had 13 taxa and 320 organisms/m . As in 1992, Tubificidae was the dominant
taxon (28 percent) and the chironomid Zalutschia zalutschicoia was the second most abundant (18 percent).
Reduced diversity, few EPT taxa, and an abundance of tubificids resulted in the forebay and
transition zone communities receiving poor ratings were . The transition zone was further impacted because
relatively few long-lived taxa were present.
Aquatic Macrophytes—The 246 acres of aquatic macrophytes on Tellico Reservoir were most
abundant in the Tellico River portion (between miles 1 and 13) of the reservoir and along the Little
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Tennessee River portion from LTRM 9 to 15. Eurasian watermilfoil was the dominant submersed
macrophyte on Tellico Reservoir.
Fish Assemblage—Electrofishing (30 transects) and gill netting samples (24 net-nights) in the
transition zone and forebay produced 1,498 individuals of 36 species. More fish (66 percent) as well as
more species (31 compared to 29) were found in the forebay than in the transition zone. Gizzard shad
comprised 37 percent of the total sample, followed by spotfin shiners, bluegill, and the black basses
(smallmouth, spotted, and largemouth) all at 9 percent. Electrofishing and gill netting results indicated most
species were present in higher numbers in the forebay than the transition zone. Walleye and sauger were
more numerous in 1993 than in previous years, which may be of interest to sport anglers in the future.
The Reservoir Fish Assemblage Index (RFAI) rated the littoral fish community (based on
electrofishing results) fair in both the forebay (RFAI=34) and transition (RFAI=38) zones. All metric
scores for both zones were identical with the exception of percent tolerant and omnivorous species which
received higher scores in the transition. Gill netting RFAI's rated the forebay (RFAI=34) fair and the
transition (RFAJ=22) poor, due primarily to lower scores for the number of species, number of sucker,
intolerant, lithophilic spawning species, and percent anomalies and dominance by a single species. Gill
netting RFAI values were not calculated for inflow zones of run-of-the-river reservoirs due to low numbers
of replicate samples.
Combined electrofishing and gill netting RFAI scores rated the forebay (RFAI=34) fair and the
transition (RFAI=30) zone poor The RFAI rating of poor in the transition resulted from a low gill netting
RFAI (22) which was the lowest score observed for run-of-the-river reservoirs in 1993. (Note: Results
from biomonitoring on Tellico Reservoir were compared to results from mainstream reservoirs because of
the lack of a deep drawdown as occurs in storage impoundments and the presence of a navigation lock
allowing recruitment of fish species.)
Summary of 1993 Conditions - Use Suitability
Fecal Cohform Bacteria—No bacteriological studies were conducted at recreation sites in 1993.
Fecal coliform bacteria concentrations were very low (geometric mean <20/100 ml) at the Vital Signs
stations. The highest individual concentrations were April samples, 114 and 54/100 ml, at the forebay and
transition zone, respectively.
Fish Tissue—An advisory not to eat catfish from Tellico Reservoir has been in effect for several
years. Documentation of the PCB problem in what was thought to be a background study in 1985 came as
a surprise because there was basically no industrial development in the watershed. Subsequently, more
intensive studies supported the initial results and showed very little change in concentrations during the late
1980s Several attempts at locating potential sources were fruitless and the source remains unknown. A less
intensive sampling effort was begun in autumn 1990. Since then one composite of five channel catfish has
been collected annually from the forebay and one from an area about 10 miles upstream (several miles
downstream of the transition zone) to continue examination of the temporal trend in PCB concentrations.
Channel catfish samples collected in autumn 1992 had relatively high PCB concentrations -
2.7 (jg/g at the forebay and 1 9 (ig/g at the mid-reservoir location. Chlordane concentrations were also
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relatively high - 0.22 and 0.20 ng/g, respectively. Other organics were either not detected or found in very
low concentrations. Arsenic, cadmium, lead, and selenium were not detected in either sample. Mercury
concentrations were relatively high - 0.65 and 0.36 (jg/g at the forebay and mid-reservoir locations. Due to
these high concentrations of mercury, largemouth bass were collected along with channel catfish in autumn
1993; results were not available at the time this report was prepared.
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Fontana Reservoir
Summary of Conditions in 1993 - Ecological Health
Water—Average flow through Fontana Reservoir in 1993 was about 107 percent of normal, with
an average residence time of 174 days Fontana Reservoir was strongly stratified, with a maximum
temperature difference in the water column at the forebav of 21.8°C in July, and remaining 14.3°C in
October. Due to the fall drawdown, the two mid-reservoir sampling locations were weakly stratified in
September and mixed in October. Maximum surface temperatures were 27.8°C at the forebay, 29.8°C at
the Little Tennessee River mid-reservoir station, and 29.0°C at the Tuckasegee River mid-reservoir station.
The maximum temperatures were in July. North Carolina's standard for maximum temperature of Class°C
waters is 29°C. Depleted DO (<2 0 mg/1) only developed at the forebay at depths of over 100 meters in
September and October. Depleted DO conditions also occurred at the Tuckasegee River mid-reservoir
station in August and September, but not in the Little Tennessee River mid-reservoir station. The DO
rating in the reservoir ecological health index was good for the forebay and Little Tennessee River mid-
reservoir sites and poor for the Tuckasegee site.
Conductivities were generally in the 20 to 30 ^mhos/cm range, the second lowest of the tributary
reservoirs, with little stratification except for late summer when a maximum conductivity of 39 (jmhos/cm
occurred. The minimum pH was 6 0 at all three sites, the maximum was 8.8 in June at the Little Tennessee
River mid-reservoir station.
Total nitrogen concentrations at the three stations were the third, fourth, and fifth lowest
concentrations of the 33 tributary reservoir stations Total nitrogen concentrations at the three sites
averaged 0.21 mg/1 in April, mostly as nitrates, and 0.07 mg/1 in August, mostly as organic nitrogen. Total
phosphorus concentrations were 0.01 mg/1 at both mid-reservoir locations and 0.003 mg/1 at the forebay in
April, and dropped to an average of 0 003 mg/1 at the three locations in August Total phosphorus
concentrations at the forebay were the lowest concentrations of the tributary reservoir stations. Total
organic carbon concentrations averaged 0.8 mg/1 in April and 1.4 mg/1 in August, with little variation
between locations. Chlorophyll a concentrations averaged 1.4 fig/1 at the forebay, and 2.7 and 2.4 fj.g/1 at
the Little Tennessee and Tuckasegee River mid-reservoir locations, respectively. These were the fourth,
fifth, and sixth lowest concentrations of the tributary reservoir stations, and were within the range
considered fair. Secchi depths at the mid-reservoir stations varied from 2.1 meters in April to 4.9 meters in
June, both in the Tuckasegee River. The water at the forebay was the clearest of all tributary reservoir
stations, ranging from 5 1 meters in September to 8.1 meters in June.
Sediment—Chemical analyses and toxicity testing of sediments were conducted on sediment
samples collected at three locations in Fontana Reservoir in 1993: a forebay site (LTRM 62.0); a mid-
reservoir site on the Tuckasegee River (TkRM 3.0) arm; and, a mid-reservoir site on the Little Tennessee
River (LTRM 81.5) arm. The presence of chlordane was detected in the forebay (12 (ig/kg) and in the
Tuckasegee River mid-reservoir region (14 (ig/kg). Toxicity tests detected acute toxicity to daphnids
(60 percent survival) and rotifers (55 percent survival) in the forebay. Particle size analysis showed
sediments in the forebay were 75 percent silt and clay, 25 percent sand; in the Little Tennessee River mid-
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reservoir were 94 percent silt and clay; and in the Tuckasegee River mid-reservoir were 76 percent silt and
clay, 24 percent sand.
Sediment quality ratings used in the overall Fontana Reservoir ecological health evaluation for
1993 were poor at the forebay (presence of chlordane and toxicity to test animals); good at the Tuckasegee
mid-reservoir site (presence of chlordane); and excellent at the Little Tennessee mid-reservoir site
Benthic Macromvertebrates—The first year that the benthic macroinvertebrate community was
evaluated on Fontana Reservoir was 1993. The benthic community at the forebay site rated very poor, the
Tuckasegee River mid-reservoir site rated poor, and the Little Tennessee River mid-reservoir site rated fair.
2
The forebay had 1,040 organisms/m representing 4 taxa. The Tuckasegee site had 15 taxa and by far the
2
greatest density of all three sites sampled (6,328 organisms/m ). The Little Tennessee mid-rcservoir site
2
had the greatest diversity of the three sites, with 23 taxa and 3,753 organisms/m . The dominant taxon at
all three sites was Tubificidac, accounting for 90 percent of the total at the forebay and Tuskasegee inflow,
and 77 percent of the total at the Little Tennessee River inflow.
The three sites sampled on Fontana Reservoir had several common problems: an absence of long-
lived taxa, an absence of EPT taxa, and an abundance of tubificids. It is also worthy to note that a common
observation at all three locations on Fontana was low numbers of chironomids. In addition to the above
elements, the forebay benthic community was further impacted by very low diversity. The Little Tennessee
mid-rcservoir site had greater diversity and fewer tubificids than the other two sites which allowed it to
receive the best overall benthic rating.
Fish Assemblage—Shoreline electrofishing (45 transects) and offshore experimental gill netting
(36 net-nights) yielded 1782 individuals with 22 species represented. Green sunfish and smallmouth bass
were the most abundant species collected, comprising 39 and 16 percent of the total sample, respectively
Bluegill (7 percent) and white bass (7 percent) were also frequently encountered. Catch rates for both gill
netting and electrofishing were approximately the same for all three sample areas (forebay, Little Tennessee
River transition, and the Tuckasegee River transition).
The Reservoir Fish Assemblage Index (RFAI) rated the littoral fish community (based on
electrofishing results) poor in all three sample areas (forebay RFAI=28, Little Tennessee River transition
RFAI=28, and Tuckasegee River transition RFAI=22) of Fontana Reservoir. All electrofishing metrics
received low to moderate scores except for percent omnivores and insectivores. Gill netting RFAI results
rated the forebay zone (RFAI=36) fair, and both the Little Tennessee River transition (RFAI=42) and the
Tuckasegee River transition (RFAI=48) zones good. Combined electrofishing and gill netting RFAI scores
rated all three zones of Fontana Reservoir fair.
Summary of Conditions in 1993 - Use Suitability
Fecal Cohform Bacteria—There were no bacteriological studies conducted on Fontana Reservoir
in 1993.
Fish Tissue—Five channel catfish were collected in autumn 1992 from both the forebay and mid-
reservoir site on the Little Tennessee River Fillets were composited by area and analyzed for selected
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metals, pesticides, and PCBs on EPA's priority pollutant list. Most analytes were not detected or had low
concentrations. Exceptions to this were mercury at both locations (0.40 (ig/g at the forebay and 0.53 ng/g
at the mid-reservoir site), and PCBs at the forebay (1.1 |ig/g). PCBs were not detected in the sample from
the mid-reservoir site. Channel catfish were collected again in 1993 from both locations and analyzed for
the same analytes with close attention for PCBs at the forebay. Largemouth bass were also collected in
autumn 1993 from both locations to further examine mercury concentrations. Results were not available at
the time this report was prepared.
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Little Tennessee River Stream Monitoring Site
Summary of 1993 Conditions - Ecological Health
Water—The water of the Little Tennessee River is soft (average hardness of 7 mg/1) and slightly
alkaline (average total alkalinity of 10 mg/1). The median pH for the stream monitoring site was 7.5. The
river was well oxygenated with dissolved oxygen levels ranging from 95 to 110 percent of saturation.
Of the 12 streams monitored across the Tennessee Valley, the Little Tennessee River ranked among
the lowest in average concentrations of organic nitrogen (0.188 mg/1), nitrate+nitrite-nitrogen (0.14 mg/1),
total phosphorus (0.030 mg/1), and dissolved orthophosphate (0.006 mg/1). The highest average
concentration of ammonia nitrogen (0.138 mg/1) was found at this site. The good total phosphorus and
nitrate+nitrite-nitrogen concentrations yielded a good rating for nutrients at the site.
Seven analyses for priority pollutant metals (dissolved cadmium, lead, nickel, silver, and zinc and
total and dissolved copper and zinc) were performed bi-monthly. Dissolved cadmium was detected in 4 of 6
samples. Three of the samples exceeded the EPA guidelines for both chronic and acute toxicity to aquatic
life. Another sample exceeded the guideline for chronic toxicity. Dissolved lead exceeded the guideline for
chronic toxicity. (Chronic toxicity bioassays are not routinely performed at stream monitoring sites As
seen below, there was no acute toxicity testing apparent in these samples.)
Sediment—Sediment quality rated good in 1993 with no acute toxicity observed and no metals,
PCBs, or pesticides exceeding the EPA guidelines.
Benthic Macroinvertebrates—In 1993, benthic macroinvertebrate results were rated good with a
2
Modified Benthic Index of Biotic Integrity (MBIB1) of score 44, with 92 taxa and 11,086 organisms/m .
2
Conditions in 1992 also rated good (MBIBI score 46) with 84 taxa and 9,079 organisms/m . Dominant
organisms in 1993 were dipteran midge larvae (54 percent), nutrient tolerant oligochaete worms
(15 percent), and caddisflies (9 percent). Mayflies were the most dominant group in 1992 (27 percent),
followed by dipteran midge larvae (23 percent) and caddisflies (19 percent). Conditions have essentially
remained unchanged between sampling years, however, an increase was noted in the numbers of silt and
nutrient tolerant organisms.
Fish Community Assessment—The fish community rated excellent with an Index of Biotic Integrity
(TBI) of 58 and showed little change since rating borderline good (IBI = 56) in 1992. With the exception of low
fish density (catch rate), measures of the fish community indicated nearly optimum conditions. Siltation, however,
was conspicuous and is suspected of effecting low fish density at this station.
Summary of 1993 Conditions - Use Suitability
Fecal Cohform Bacteria—No studies conducted in 1993.
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Fish Tissue—A five fish composite each of river redhorse, channel catfish, and largemouth bass
were collected during summer 1992 and analyzed for selected metals, pesticides, and PCBs. All analytes
were either not detected or found in low concentrations.
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FRENCH BROAD RIVER WATERSHED
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Douglas Reservoir
Summary of 1993 Conditions - Ecological Health
Water—During the summer of 1993, surface water temperatures ranged from 13 .4°C in April to
28.5°C in July at the forebay, and from 15.4°C to 30.2°C (for the same months) at the mid-reservoir
sampling location. Some thermal stratification was observed beginning in May at both the forebay and mid-
reservoir locations, and was strongest in July when the temperature differentials between the bottom and the
surface were 15.1°C at the forebay, and 12.1°C at the mid-reservoir location. This stratification existed
through August at the mid-reservoir location, and through September at the forebay.
Dissolved oxygen at the 1.5m depth ranged from 12.5 mg/1 in May to 4.6 mg/1 in October at the
forebay, and from 11.8 mg/1 in May to 5.5 mg/1 in September at the mid-reservoir location. (The State of
Tennessee's minimum dissolved oxygen criteria for the protection of fish and aquatic life is 5 mg/1, at the
1.5m depth.) Anoxic conditions near the bottom existed from June through September at the forebay, and
from June through August at mid-reservoir. This hypolimnctic anoxia peaked at the forebay in August and
at the mid-reservoir in July. In each case, about two-thirds of the water column had dissolved oxygen
concentrations of less than 1 mg/1. The forebay and mid-rcscrvoir sampling sites had, respectively, about
30% and 20% of their cross-sectional areas (six-month summertime average) with dissolved oxygen
concentration less than 2.0 mg/1; and, over 60% of each site's cross-sectional bottom length (six-month
summertime average) had a dissolved oxygen concentration less than 2.0 mg/1. Because of the conditions
described above (and the low surface concentration in October at the forebay, 4.6 mg/1), DO ratings used in
the overall reservoir ecological health evaluation for Douglas Reservoir were very poor at both the forebay
and at the mid-reservoir sampling locations.
Values of pH ranged from 6.6 to 9.4 for both locations in Douglas Reservoir in 1993. In April
through August at the forebay, and May through August at the mid-rescrvoir location, near surface pH's
equal to or exceeding 8.5 were observed. In almost all of these cases, when the pH was above 8.5, surface
dissolved oxygen saturation values exceeded 100 percent, indicating high levels of photosynthesis
In 1993, the average concentrations of total phosphorus (average 0.035 mg/1 at the forebay and
0.040 mg/1 at the mid-rcservoir) were higher in Douglas Reservoir than any of the other tributary Vital
Signs reservoirs; and, at the mid-rcscrvoir sampling location the dissolved ortho phosphorus (average
0.013 mg/1) was also higher than any of the other tributary reservoirs. The Douglas mid-rescrvoir sampling
site historically has had the lowest average TN/TP ratios of all the tributary reservoirs.
In 1993, concentrations of chlorophyll a averaged 6.6 jo.g/1 at the forebay and 10.3 (j.g/1 at the mid-
rcservoir site. These concentrations are somewhat lower than those measured in 1992, when they were
among the highest of the Vital Signs reservoirs. The chlorophyll a ratings used in the 1993 ecological
health evaluation for Douglas Reservoir were good at the forebay (i.e. falling in the 3 to 10 (a.g/1 range); and
fair at the mid-reservoir location (i e. falling in the 10 to 15 (ag/1 range)
The water of Douglas Reservoir, especially in the mid-rcservoir area has historically had low water
clarity In 1993, the Secchi depth averaged only 1.2 m, the lowest of all the tributary reservoir sampling
locations.
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Sediment—Chemical analyses of sediments in Douglas Reservoir in 1993 indicated the presence of
chlordane (18 ng/kg) at the mid-reservoir site. Toxicity tests detected acute toxicity to rotifers (55 percent
survival) in the mid-reservoir. Particle size analysis showed sediments from the forebay were about
100 percent silt and clay and from the mid-reservoir were 83 percent silt and clay, 17 percent sand.
Sediment quality ratings used in the overall Douglas Reservoir ecological health evaluation for
1993 were excellent at the forebay; and poor at the mid-reservoir site (presence of chlordane and toxicity to
rotifers).
Benthic Macroinvertebrates—The forebay on Douglas Reservoir did not change significantly from
2
the previous year. Only 265 organisms/m representing 6 taxa were found, similar to the number of taxa
2
(7) and density (282 organisms/m ) found in 1992. The dominant taxa were Chironomus (50 percent) and
Tubificidae (31 percent). The benthic macroinvertebrate community at this site was poor primarily because
of the absence of long-lived and EPT taxa, and because of the abundance of chironomids. The benthic
community structure observed at the forebay is indicative of low near-bottom dissolved oxygen
concentrations.
The inflow site on Douglas Reservoir was not evaluated in 1993 because it was determined that
90 percent of the samples taken at that site were above the average winter pool level.
Fish Assemblage—Shoreline electrofishing (30 transects) and offshore/deep netting (24 net-nights)
samples collected 2,679 fish of 29 species. The most abundant species were gizzard shad (29 percent),
followed by white bass (20 percent), and largemouth bass (13 percent). The crappie species (black and
white) represented 10 percent of the total sample. Electrofishing results indicated fish abundance in the
transition (1,075) was twice that of the forebay (533) due mainly to much higher numbers of white bass,
largemouth bass, and white crappie. Gill netting efforts showed a similar pattern, with the transition catch
(884) considerably higher than the forebay (187). The only species that were more abundant in the forebay
samples were smallmouth buffalo and black crappie.
The Reservoir Fish Assemblage Index (RFAI) analysis of shoreline electrofishing data showed the
forebay (RFAI=42) zone to be good and the transition (RFAI=36) fair. Maximum metric scores were
recorded at both sample areas for species diversity, number of sucker species, and dominance by a single
species, and minimum scores for percent insectivores The gill netting RFAI rated the transition zone
(RFAI=50) good and the forebay (RFAI=30) poor. Transition zone scores were midrange or maximum (3's
or 5's) for all metrics except for number of intolerant species. Combined electrofishing and gill netting
RFAI scores indicated good fish community conditions in the transition (RFAI=43) zone and fair in the
forebay (RFAI=36).
Summary of Conditions in 1993 - Use Suitability
Fecal Cohform Bacteria—One swimming beach and two boat ramps were tested for fecal
coliform bacteria twelve times in 1993 Two samples were collected within 48-hours of a rainfall of at least
one-half inch. Fecal coliform bacteria concentrations were very low (geometric mean <20/100 ml) at every
site.
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Fish Tissue—TVA worked with the Tennessee Department of Environment and Conservation in
1992 to conduct fish tissue studies on Douglas Reservoir TVA collected the fish samples and provided
fillets to TDEC for analysis. Results were not available at the time this report was prepared
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French Broad River Stream Monitoring Site
Summary of 1993 Conditions - Ecological Health
Water—The water of the French Broad River is soft (average hardness of 18 mg/1) and only
slightly alkaline (average total alkalinity of 20 mg/1), reflecting the underlying geology of the area The
median pH for the stream monitoring site was 7.4. The river was well oxygenated with dissolved oxygen
levels ranging from 87 to 99 percent of saturation.
Of the 12 streams monitored across the Tennessee Valley, the French Broad River station ranked
among the highest in mean concentrations of total phosphorus (0.122 mg/1), dissolved orthophosphate
(0.087 mg/1), and nitrate+nitrite-nitrogen (0.56 mg/1). Average concentrations of 0.220 mg/1 and 0.030 mg/1
for organic nitrogen and ammonia nitrogen placed the site near median for these variables. The high
average total phosphorus concentration yielded a poor rating for nutrients at the site.
Seven analyses for priority pollutant metals (dissolved cadmium, lead, nickel, silver, and zinc and
total copper and zinc) were performed bi-monthly. Dissolved cadmium was detected in 5 of 6 samples.
Three of those exceeded the EPA criterion for chronic toxicity to freshwater aquatic life. (Chronic toxicity
bioassays are not routinely performed at stream monitoring sites However, the acute toxicity test data is
consistent with the water chemistry. See "Sediment" for additional information on toxicity testing results.)
Sediment—Sediment quality rated good in 1993 with no acute toxicity observed and no metals,
PCBs, or pesticides exceeding the EPA guidelines This is an improvement over 1992 when sediment
quality rated fair
Benthic Macroinvertebrates—In 1993, benthic macroinvertebrates rated fair with a Modified
2
Benthic Index of Biotic Integrity (MBIBI) score of 36, with 77 taxa and 12,121 organisms/m . Conditions
2
in 1992 also rated fair (MBIBI score 35) with 81 taxa and 10,961 organisms/m . Benthic organisms have
essentially remained unchanged between sampling years. Dominant organisms in 1993 were dipteran midge
larvae (67 percent), caddisflies (15 percent), and dipteran black-fly larvae (6 percent). Dipteran black-fly
larvae was the most dominant organism in 1992 (49 percent), followed by dipteran midge larvae (36
percent) and caddisflies (5 percent). The French Broad River consistently ranks the poorest of the 12
stream monitoring sites. Siltation from agricultural land usage along the river severely affects benthic
communities at this site.
Fish Community Assessment—The fish community continued to be depressed rating borderline
poor with an Index of Biotic Integrity (IBI) score of 38 in 1993 and borderline poor (IBI = 36) in 1992.
Serious problems were found in species richness and composition, and in fish density, indicating poor
conditions Forty to 60 native species were expected to occur at this station, but only 30 were found.
Diversity was low among darters, sunfish, suckers, and intolerant species. The proportion of tolerant fish
was excessive representing approximately 41 percent of the fish found, and fish density was among the
lowest found at the 11 stations sampled in 1993. Turbidity, siltation, and nutrient enrichment were evident
and probably played some part in the disorder exhibited by the fish community.
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Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—No bacteriological studies were conducted in this watershed by TVA in
1993.
Fish Tissue—A five fish composite each of carp, channel catfish, and largcmouth bass were
collected during summer 1992 and analyzed for selected metals, pesticides, and PCBs. All analytes were
not detected or found in low concentrations.
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Nolichucky River Stream Monitoring Site
Summary of 1993 Conditions - Ecological Health
Water—The water of the Nolichucky River is moderately hard (average hardness of 79 mg/l) and
moderately alkaline (average total alkalinity of 67 mg/l). The median pH for the stream monitoring site was
7.8. The river was well oxygenated with dissolved oxygen levels ranging from 87 to 100 percent of
saturation.
Of the 12 streams monitored across the Tennessee Valley, the Nolichucky River station ranked just
above the median concentrations for average organic nitrogen (0.223 mg/l), nitrate+nitrite-nitrogen
(0.56 mg/l), total phosphorus (0.075 mg/l), and dissolved orthophosphate (0.024 mg/l). An average
concentration of ammonia nitrogen of 0.022 mg/l placed the site among the best for the variable. The
moderately high average total phosphorus concentration yielded a fair rating for nutrients at the site.
Seven analyses for priority pollutant metals (dissolved cadmium, lead, nickel, silver, and zinc and
total copper and zinc) were performed bi-monthly Dissolved cadmium was detected in 5 of 6 samples.
Dissolved lead was detected in 2 of 6 samples. Neither metal exceeded the EPA criteria for protection of
aquatic life or human health Additional metals analyses included both total and dissolved forms of
manganese and iron. Total iron exceeded the chronic toxicity criterion for freshwater aquatic life in one
sample and the criterion for combined consumption of fish and water in 4 samples. Total manganese was
detected in 5 of 6 samples, although only one sample exceeded an EPA criterion value (for combined
consumption of fish and water).
Sediment—Sediment quality rated good in 1993 with no acute toxicity observed and no metals,
PCBs, or pesticides exceeding the EPA guidelines This is a significant improvement over 1992 when
sediment quality rated poor.
Benthic Mcicroinvertebrates—In 1993. benthic macroinvertebrates rated fair with a Modified
2
Benthic Index of Biotic Integrity (MBIB1) of score 39, with 81 taxa and 5,543 organisms/m . Conditions
2
in 1992 were also rated fair (MBIBI score 39) with 91 taxa and 6,195 organisms/m . Dominant organisms
in 1993 were dipteran midge larvae (32 percent), caddisflies (24 percent), and mayflies (19 percent).
Diptcran midge larvae were also the most dominant group in 1992 (46 percent), followed by dipteran
black-fly larvae (18 percent) and caddisflies (14 percent). Conditions have essentially remained unchanged
between sampling years. Siltation from agricultural land usage along the river and mica and mica and
feldspar mining in the watershed adversely affect benthic communities at this site.
Fish Community Assessment—The fish community rated good with an Index of Biotic Integrity
(IBI) score of 48, improving considerably from the borderline fair (IBI = 38) rated in 1992. Improvement
included a lower proportion of tolerant fish, a higher proportion of piscivorous fish, increased fish density,
and absence of hybrids. Deficiencies in number of native species and in numbers of darter, sunfish, and
intolerant species continued to indicate poor conditions. Excessive turbidity and heavy siltation have been
observed at this station during all sampling trips, 1990-93.
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Summary of 1993 Conditions - Use Suitability
Fecal Coliform Bacteria—Bacteriological studies were not conducted in this watershed by TVA in
1993.
Fish Tissue—A five fish composite each of carp, channel catfish, and largemouth bass were
collected during summer 1992 and analyzed for selected metals, pesticides, and PCBs. All analytes were
not detected or found in low concentrations.
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HOLSTON RIVER WATERSHED
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Cherokee Reservoir
Summary of 1993 Conditions - Ecological Health
Water—Summer surface water temperatures ranged from 12.2°C in April to 29.8°C in July at the
forebay, and from 14.4°C to 30.9°C for the same months at the mid-reservoir sampling location
(Tennessee's maximum temperature criterion for the protection of fish and aquatic life is 30.5C). Thermal
stratification was evident in Cherokee Reservoir in 1993. Stratification was strongest in June, when the
temperature difference between the surface and the bottom of the reservoir was about 20°C at the forebay
and about 18°C at the mid-reservoir location. Thermal stratification persisted through September at the
forebay and through August at the mid-reservoir site
Dissolved oxygen at the l 5m depth ranged from 15.2 mg/1 (algal bloom) in April to 5.2 mg/1 in
September at the forebay. and from 14.2 mg/1 (algal bloom) in April to 5.6 mg/1 in July at the mid-reservoir
sampling location. Anoxic conditions in the hypolimnion developed in the forebay in July and existed
through October In July and August, dissolved oxygen concentrations were less than 1 mg/1 for about
three-fourths of the water column. Dissolved oxygen gradients (DO's) were high in the forebay (about
7 mg/1) in June, July, and August. The gradients were not as high in September and October because of the
low surface dissolved oxygen. Similar conditions existed at the mid-reservoir sampling location where
hypolimnetic anoxia existed near the bottom in July and August In July in the mid-rescrvoir location,
three-fourths of the water column contained less than 1 mg/1 dissolved oxygen. Dissolved oxygen gradients
of 9.4 mg/1 and 7 6 mg/1 were observed in June and August, respectively Such a high gradient did not exist
in July because of the low surface dissolved oxygen for that month The forebay and mid-reservoir
sampling sites both had over 20% of their cross-sectional areas (six-month summertime average) with
dissolved oxygen concentration less than 2.0 mg/1, and, over 40 percent of each site's cross-sectional
bottom length (six-month summertime average) had a dissolved oxygen concentration less than 2.0 mg/1.
Because of the conditions described above, DO ratings used in the overall reservoir ecological health
evaluation for Cherokee Reservoir were very poor at both the forebay and at the mid-reservoir sampling
locations.
In 1993, values of pH in Cherokee Reservoir ranged from 6.9 to 8.8 for both monitoring locations.
Surface water pH values slightly exceeded 8.5 (Tennessee's maximum pH criterion for the protection of
fish and aquatic life is 8 5) at the forebay in April through August, and at the mid-reservoir location in May
through August. In each of these cases, with the exception of July at the mid-reservoir section, high
dissolved oxygen saturation values coincided with the high pH's, sometimes up to 140 percent, indicating
substantial photosynthetic activity.
Historically, the mid-reservoir sampling site has had the highest nutrient concentrations among all
reservoir Vital Signs sampling locations. Average nutrient concentrations at the mid-reservoir location in
1993 were observed to be only about half of 1992 concentrations In 1993, the average total nitrogen
concentration was 0.45 mg/1 and the average total phosphorus concentration was 0.030 mg/1. Lower
nutrient concentrations at the forebay as well as higher TN/TP ratios indicate a higher productivity
potential at the mid-rescrvoir sampling site than at the forebay sampling site
Concentrations of chlorophyll a support this hypothesis where chlorophyll a averaged 7.6 (ig/1 at
the forebay and 9.4 \isj\ at the mid-reservoir site. The chlorophyll a ratings used in the 1993 ecological
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health evaluation for Cherokee Reservoir were good (i.e. falling in the 3 to 10 fig/1 range), at both the
forebay and the mid-reservoir locations
Sediment—Chemical analyses of sediments in Cherokee Reservoir in 1993 indicated high levels of
copper (57 mg/kg) from the mid-reservoir and elevated levels of un-ionized ammonia from both the forebay
(390 fag/1) and mid-rcservoir (290 fag/1). Toxicity tests detected acute toxicity to rotifers (75 percent
survival) in the mid-reservoir. Particle size analysis showed sediments from the forebay were about
100 percent silt and clay and from the mid-reservoir were 99 percent silt and clay.
Sediment quality ratings used in the overall Cherokee Reservoir ecological health evaluation for
1993 were good at the forebay (presence of ammonia); and poor at the mid-reservoir site (presence of
copper and ammonia and toxicity to rotifers).
Benthic Macroinvertebrates—In 1993, the overall condition of the benthic macroinvertebrate
community in the forebay of Cherokee Reservoir remained approximately the same as in 1992. However,
2
there was a slight increase in taxa (14) and decrease in density (510 organisms/m ). As in 1992,
Tubificidae (45 percent) and Chironomus sp (26 percent) were the dominant taxa.
The forebay had a fair macroinvertebrate benthic community; problem characteristics were
numbers of long-lived species and the abundance of chironomids. On a more positive note, this site
exhibited excellent species diversity The Cherokee inflow benthic macroinvertebrate community improved
substantially since last year, resulting in an excellent rating. The only factor that kept this site from
receiving a perfect score for the benthic component was a slightly elevated number of chironomids in the
sample The abundance of mayfly Hexagenia hmbata. considered to be an intolerant, long-lived species,
greatly improved the benthic community rating at the inflow.
Fish Assemblage—Fish sampling in shoreline (45 electrofishing transects) and offshore/deep areas
(34 net-nights) of Cherokee Reservoir produced a total of 4,086 individuals including 33 species. The most
numerous species was gizzard shad (35 percent), followed by bluegill (20 percent), and largemouth bass
(14 percent) Species richness ranged from 24 in the transition , 25 in the forebay, to 27 in the inflow.
Electrofishing results indicated higher abundance in the inflow (1,458), where gizzard shad and largemouth
bass were most numerous, and in the forebay (1,104) where bluegill numbers were very high. Gill netting
catch rates were progressively higher from inflow to forebay areas due largely to abundance of gizzard
shad, quillback carpsuckers, and striped bass.
The Reservoir Fish Assemblage Index (RFA1) analysis of shoreline electrofishing data determined
the quality of the littoral fish communities of the forebay (RFAI=32) and inflow (RFAI=34) zones to be
fair and the transition (RFA1=30) to be poor. All three reservoir sample areas were rated fair based on gill
netting RFAI's. Combined electrofishing and gill netting RFAI scores for the forebay (RFAI=36), transition
(RFAI=34), and inflow (RFAI=35) zones of Cherokee Reservoir were all rated fair.
Summary of Conditions in 1993 - Use Suitability
Fecal Coliform Bacteria—One swimming beach, seven boat ramps, and the head of one small
embayment were tested for fecal cohform bacteria twelve times in 1993. Two samples were collected
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within 48-hours of a rainfall of at least one-half inch Fecal coliform bacteria concentrations were vers' low
(geometric mean <20/100 ml) at the swimming beach and at six of the boat ramps. At the Malinda Bridge
boat ramp and at the head of Spring Creek Embayment, the geometric mean fecal coliform concentrations
were between 20 and 50/100 ml, well below the Tennessee criterion for recreation.
Fish Tissue—Channel catfish were collected from Cherokee Reservoir as part of screening studies
in autumn 1992 Results indicated low or nondetectable concentrations of metals. Mercury, known to be a
problem in the North Fork Holston River, was 0.29 jj.g/g at the forebay with lower concentrations at the
other two locations. The only organics found were PCBs and chlordane. Chlordane concentrations were
low (maximum 0.07 j-ig/g) and PCB concentrations were generally similar to those in past years - 0.8, 0.5,
and 0.5 fxg/g at the forebay, transition zone, and inflow, respectively.
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Fort Patrick Henry Reservoir
Summary of Conditions in 1993 - Ecological Health
Water—Average flow through Fort Patrick Henry Reservoir in 1993 was about 91 percent of
normal. It is only stratified due to the continual release of cold water from the three upstream dams. The
maximum temperature difference in the water column was 12.5°C in July. The maximum surface
temperature was 27.8°C in July, well below Tennessee's maximum temperature criterion for aquatic life of
30.5°C. Low DO (<5.0 mg/1) conditions developed in July, August, and October, but DO never dropped
below 2.2 mg/1. Absence of DO <2.0 mg/1 gave Fort Patrick Henry Reservoir a good rating for DO in the
reservoir ecological health index.
Conductivities varied widely from month to month and in the water column, but averaged the
fourth highest of the 19 tributary reservoirs. The minimum was 150 (Amhos/cm at the bottom of the water
column in May, and the maximum was 216 nmhos/cm in September, also at the bottom of the water
column. Surface pH reached or exceeded 9.0 in July, August, and September, while bottom pH never fell
below 7.1.
Relatively high nutrient concentrations were found: the total nitrogen concentration in April was
1.08 mg/1, 72 percent as nitrates, and 0.63 mg/1 in August, 62 percent as organic nitrogen. Total
phosphorus concentrations were 0.02 mg/1 in both surveys. Total organic concentrations were 2.0 mg/1 in
April and 2.8 mg/1 in August Chlorophyll a concentrations tied for the fourth highest of the 33 tributary
reservoir stations, averaging 10.3 |ig/l. This chlorophyll concentration was considered fair in the reservoir
ecological health index. Water clarity was low. Sccchi depths ranged from 1.3 meters in September to
1.7 meters in July and August.
Sediment—Chemical analyses of sediments from the forebay of Fort Patrick Henry Reservoir in
1993 indicated slightly elevated levels of un-ionized ammonia (210 (ig/1). Toxicity tests detected no toxicity
to the two organisms tested. Particle size analysis showed sediments from the forebay were 99 percent silt
and clay.
The sediment quality rating used in the overall Fort Patrick Henry Reservoir ecological health
evaluation for 1993 was good at the forebay (presence of ammonia)
Benthic Macroinvertebrates—The first year that the benthic community in this tributary reservoir
was evaluated was 1993 The forebay, the only sample location, had a fair benthic macroinvertebrate
2
community with 11 taxa, 438 organisms/m , and Tubificidae as the dominant taxa (63 percent). The
absence of EPT taxa and the abundance oftubificids negatively impacted the benthic community. An
average representation of the long-lived species Corbicula fluminea. average taxa richness, and low
numbers of chironomids were all positive attributes of the benthic community.
Fish Assemblage—Only the forebay zone was sampled on Fort Patrick Henry Reservoir in fall
1993. Shoreline electrofishing (15 transects) and offshore experimental gill netting (12 net-nights) yielded
1,251 individuals represented by 22 species. Fifty-one percent of the total catch consisted of spotfin
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shiners, followed by gizzard shad (23 percent), bluegill (7 percent), carp (6 percent), and largemouth bass
(5 percent).
Fish community conditions were rated fair for both electrofishing (RFAI=38) and gill netting
(RFAI=34) in the forebay zone of Fort Patrick Henry Reservoir. The overall RFAI of 36 also rated the
reservoir forebay as fair.
Summary of Conditions in 1993 - Use Suitability
Fecal Cohform Bacteria—The boat ramp at Warriors Path State Park was tested for fecal
coliform bacteria in 1993 The geometric mean concentration was 94/100 ml, well within Tennessee's
Criterion for water contact recreation.
Fish Tissue—Autumn 1993 was the first time TVA had conducted fish tissue samples from Fort
Patrick Henry Reservoir. Results were not available at the time this report was prepared.
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Boone Reservoir
Summary of Conditions in 1993 - Ecological Health
Water—The average flow through Boone Reservoir in 1993 was about 97 percent of normal, with
an average residence time of 38.5 days. Boone Reservoir has two large arms, the South Fork Holston River
and Watauga River, their confluence is slightly more than one mile upstream of Boone Dam. Both arms
receive cold water releases from the deep impoundments upstream. Consequently, Boone Reservoir remains
stratified throughout the sampling period, with a maximum temperature difference in the water column at
the forebay of 16.3°C in July. The maximum surface temperature was 28.9°C at the forebay in July, well
below Tennessee's maximum temperature criterion for aquatic life of 30.5°C. DO depletion (DO <2.0 mg/1)
at the forebay and in the South Fork Holston River arm was limited to the metalimnion from July through
October. In the Watauga arm, DO depletion occurred at the bottom in September. The limited amount of
DO depletion gave the forebay a good rating and both mid-reservoir stations fair ratings for DO in the
reservoir ecological health index
Conductivities varied widely by month and depth. In the Watauga arm, conductivities ranged from
74 |imhos/cm at the bottom in May to 236 ^mhos/cm in the metalimnion in September. In the South Fork
Holston River arm, conductivities varied from 177 (imhos/cm at the surface to 264 ^mhos/cm in the
metalimnion in July. Conductivities in the forebay reflected the mixing of these two rivers. The minimum
pH was 6.7 in the Watauga arm in September, while pH reached 9.1 in both the forebay and Watauga arm
in the summer.
Total nitrogen concentrations on South Fork Holston River were the third highest of the 33
tributary reservoir stations. Total nitrogen concentrations in April ranged from 0.76 mg/1 on the Watauga
River to 1.07 mg/1 on South Fork Holston River. About 60 percent of the total nitrogen was nitrates at each
site. Nitrate concentrations had dropped by August to 0.03 mg/1 or less at each station, bringing the
average total nitrogen concentration to 0.41 mg/1, slightly higher at the mid-reservoir stations than at the
forebay. Total phosphorus concentrations were 0.01 mg/1 on the Watauga River and 0.02 mg/1 at the other
two sites in April. Total phosphorus concentrations dropped at the forebay from April to August to
0.008 mg/1, remained constant in the South Fork Holston River, and increased in the Watauga River to
0.03 mg/1. Dissolved ortho phosphorus concentrations were 0.003 mg/1 in the Watauga Rjver both months
and at the forebay in April, and <0.002 for the other three samples The TN/TP ratios were high, 50:1 at
the forebay and higher at the other two stations. Total organic carbon concentrations were high, ranging
from 1 8 mg/1 in the Watauga River to 2.7 mg/1 in the forebay in April, and 3.8 mg/1 at both mid-reservoir
stations to 4 5 mg/1 at the forebay in August. The forebay concentrations of total organic carbon were the
fourth highest of the tributary reservoir locations.
The two mid-reservoir stations had the second and third highest chlorophyll concentrations of the
tributary reservoir stations. Average chlorophyll a concentrations were 8.7 fj.g/1 at the forebay, 11.9 fj.g/1 in
the South Fork Holston River, and 10.4 |a.g/l in the Watauga River. These concentrations are in the ranges
considered good for the forebay and fair for the two mid-reservoir locations in the reservoir ecological
health index. Water clarity was low at the mid-reservoir stations, Secchi depths varied from 1.0 meter in
the South Fork Holston River in June to 1.5 meters at both stations in October. The South Fork Holston
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River mid-reservoir station had the second lowest water clarity of the tributary reservoir stations. At the
forebay, Secchi depths varied from 1.3 meters in May to 2.2 meters in October.
Sediment—Chemical analyses of sediments collected from three locations in Boone Reservoir in
1993 indicated very high levels of un-ionized ammonia at all three sites: 790 (ig/1 at the forebay sampling
site, 660 jo.g/1 at the South Fork Holston River (SFHR) mid-reservoir sampling site; and, 990 p.g/1 at the
Watauga River (WR) mid-reservoir sampling site. Chlordane was also detected in sediment at all three
sampling sites: 22 (ig/kg at the forebay site; 35 (ig/kg at the SFHR mid-reservoir site, and, 35 fig/kg at the
WR mid-reservoir site. In addition, high levels of copper (58 mg/kg) and zinc (370 mg/kg) were found at
the Watauga River mid-reservoir sampling site. However, no acute toxicity to daphnids nor rotifers was
found at any of the three sampling sites. Particle size analysis showed sediments in the forebay were about
100 percent silt and clay; in the S. F. Holston River mid-reservoir were 99 percent silt and clay; and in the
Watauga River mid-reservoir were 86 percent silt and clay, 14 percent sand.
Sediment quality ratings used in the overall Boone Reservoir ecological health evaluation for 1993
were good at the forebay as opposed to excellent because ammonia was elevated; good at the SFHR mid-
reservoir site (presence of ammonia); and fair at the WR mid-reservoir site (presence of copper, zinc, and
ammonia).
Benthic Macroinvertebrates—The first year that the benthic macroinvertebrate community was
evaluated on Boone Reservoir was 1993. The forebay site had a poor benthic community, with 1,107
organisms representing a mere 10 taxa; Tubificidae (58 percent) and the tubificid Limnodrilus hoffmeisteri
(38 percent) were the dominant taxa. The South Fork Holston River and the Watauga River mid-reservoir
sites both had poor benthic communities. Both had only 11 taxa, but the South Fork Holston inflow had a
2
lower density (615 organisms/m ) than the Watauga inflow (267). The tubificids Limnodrilus sp and
Tubificidae were the dominant taxa at both mid-reservoir sites comprising 91 percent of the total at the
South Fork Holston site and 96 percent of the total at the Watauga site.
The forebay and both inflows were negatively impacted by the absence of long-lived and EPT taxa,
and the abundance of tubificids. If not for the relatively low proportion of chironomids, all sites would have
received a "very poor" benthic rating.
Fish Assemblage—Electrofishing (45 transects) and gill netting (34 net-nights) results from Boone
Reservoir yielded 2,439 individuals of 23 species. Bluegill were the most abundant species, comprising
29 percent of the total number of fish sampled. OtheT species making up a significant portion of the
reservoir sample included gizzard shad (21 percent), spotfin shiners (21 percent), and carp (9 percent). Fish
abundance was greater in the Watauga River transition zone (1,414), followed by the South Fork Holston
River transition (632) and the forebay (393). Both electrofishing and gill netting total catch rates followed
the same pattern as abundance.
The Reservoir Fish Assemblage Index (RFAI) rated the quality of the littoral community (as
determined by electrofishing samples) fair in the Holston River transition (RFA1=32) and poor in both the
Watauga River transition (RFAI=28) and forebay zones (RFAI=26). Minimum metric scores for diversity,
and number of intolerant and lithophilic spawning species were recorded for all stations. The gill netting
RFAI followed the same pattern as electrofishing, rating the Holston River transition (RFAI=36) fair, and
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both the Watauga River transition (RFAI=28) and forebay (RFAI=26) zones poor. Scoring at all zones
revealed scattered values for most metrics with the exception of maximum scores (5) for percent anomalies,
and minimum scores (1) for percent tolerant and omnivorous species.
Combined electrofishing and gill netting RFAI scores for both the forebay (RFAI=26) and
Watauga River transition (RFAI=28, which was the lowest tributary transition RFAI recorded in 1993)
rated poor and the Holston River transition zone (RFA1=34) rated fair.
Summary of Conditions in 1993 - Use Suitability
Fecal Coliform Bacteria—Two swimming areas and four boat ramps were each tested for fecal
coliform bacteria twelve times in 1993. No samples were collected within 48-hours of a rainfall of at least
one-half inch. Bacteria concentrations were very low (geometric mean <20/100 ml) at the four boat ramps.
The geometric mean fecal coliform concentration at the swimming beaches were 106 and 51/100 ml, well
within Tennessee's criterion of 200/100 ml for water contact recreation. One sample at the Boone Dam
recreation area exceeded Tennessee's maximum concentration criterion for one sample of 1000/100 ml.
Fish Tissue—Past studies conducted by the state of Tennessee found PCBs and chlordane in fish
tissue, resulting in a state issued advisory that catfish and carp should not be eaten by children, pregnant
women, and nursing mothers. Further, all other people should limit their consumption of these particular
fish Fish samples were collected by TVA in autumn 1993, but results were not available at the time this
report was prepared.
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South Holston Reservoir
Summary of Conditions in 1993 - Ecological Health
Water—The average flow through South Holston Reservoir in 1993 was near normal with an
average residence time of about 341 days. The reservoir was strongly stratified, with a maximum
temperature difference in the forebay water column of 21.9°C in July. The maximum surface temperature
was 28.3°C at the forebay in July, well below Tennessee's maximum temperature criterion for aquatic life
of 30.5°C. DO depletion (DO <2.0 mg/1) occurred in both the metalimnion and at the bottom of the water
column. Areas of DO depletion began in July at mid-reservoir and August at mid-reservoir. Because the
water was clearer at the forebay than at mid-reservoir and the photic zone was deeper, metalimnetic DO
depletion occurred at deeper depths in the forebay than at mid-reservoir and the area of low DO was not
mixed as the surface cooled in October as was the case at mid-reservoir. For the reservoir ecological health
index, DO was considered fair at the forebay and poor at mid-reservoir.
Conductivities varied widely by month and depth, from a minimum of 72 ^mhos/cm in May near
the bottom at the forebay to 270 ^mhos/cm at the mid-reservoir bottom in September. Surface pH was
between 8.5 and 9.0 at both stations each month except for April at the forebay The minimum pH was 7.1
at mid-reservoir in September
Total nitrogen concentrations were 0 75 and 1.08 mg/1 in April at the forebay and mid-reservoir,
respectively, about three-fourths as nitrates. In August, the total nitrogen concentration had dropped to
0 36 mg/I at both stations, primarily due to a decline in nitrates. The mid-reservoir total nitrogen
concentrations were the fourth highest of the 33 tributary reservoir stations. In April, total and dissolved
ortho phosphorus concentrations were 0.01 and 0.003 mg/1 at the forebay and 0.02 and 0.003 mg/1 at mid-
reservoir. In August, total phosphorus was <0.002 mg/1 at the forebay and 0.003 at mid-reservoir TN/TP
ratios were very high, over 50 in April and over 100 in August. Total organic carbon concentrations varied
only from 1.7 mg/1 in April to 2 7 mg/1 in August, both concentrations at mid-reservoir.
Average chlorophyll a concentrations were 3.4 fig/1 at the forebay and 7.0 jj.g/1 at mid-reservoir.
These concentrations are in the range considered good in the reservoir ecological health index. Secchi
depths varied from 1.6 m in April to 2.3 m in September and October at mid-reservoir and from 2.0 m in
May to 5.75 m in June at the forebay. The forebay had the fourth clearest water of the 19 tributary
reservoir forebays
Sediment—Chemical analyses of sediments in South Holston Reservoir in 1993 indicated the
presence of chlordane (12 |ig/kg) and un-ionized ammonia (310 (ig/1) in the mid-reservoir. Toxicity tests
detected no acute toxicity to daphnids or rotifers, however survival of daphnids (75 percent survival) was
reduced in the forebay Particle size analysis showed sediment in the forebay were 99 percent silt and clay,
and in the mid-reservoir were 98 percent silt and clay.
Sediment quality ratings used in the overall South Holston Reservoir ecological health evaluation
for 1993 were good at the forebay as opposed to excellent due to reduced survival of daphnids) and good at
the mid-reservoir site (presence of ammonia and chlordane).
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Benthic Macromvertebrates—The first year that the bcnthic macroinvertebrate community was
evaluated on the South Holston Reservoir was 1993. The forebay site had a very poor community, with
2
only 3 taxa, 98 organisms/m , and the tolerant Tubificidae comprising 97 percent of the total. The inflow
2
site rated somewhat better with 13 taxa and 354 organ;.r.ms/m , dominated by Tubificidae (69 percent).
The forebay site had very poor benthic community structure as indicated by low diversity, the
absence of EPT and long-lived taxa, and the preponderance of tubificids; a low number of chironomids was
the only metric that kept this site from receiving the lowest possible score. The inflow site had a fair
benthic representation, but an absence of EPT taxa and an abundance of tubificids were negative attributes
of the community. As was the case at the forebay, a low number of chironomids found at the site was a
considered a positive indicator. Diversity and the presence of long-lived species allowed the inflow site to
receive a better rating than the forebay site.
Fish Assemblage—Fish samples taken in the shoreline areas (30 electrofishing transects) and
offshore/deep areas (24 net-nights) of South Holston Reservoir produced a total of 2,160 individuals
represented by 27 species. Fish density and diversity was similar between the forebay (1,246 individuals of
20 taxa) and transition zone (914 individuals of 23 taxa) No inflow zone sample was collected from South
Holston Reservoir. The three most abundant species were spotfin shiner (46 percent), gizzard shad
(10 percent), and bluegill (8 percent). Other abundant species included black crappie and walleye at six
percent, and white bass at five percent of the total catch. Gill netting results indicated an increase from
1992 estimates in black crappie numbers in both forebay and transition zones.
RFAI analysis of electrofishing data determined the quality of the littoral fish community in the
transition zone (RFAI=40) and forebay (RFAI=38) to be fair. Gill netting RFAI rated the transition
(RFAI=32) fair and forebay (RFAI=50) good. Forebay scores for all metrics were maximum except for
number of sunfish and sucker species, and percent insectivores. The forebay score of 50 represented a
substantial improvement from the previous sample season (1992 RFAI=28). Combined electrofishing and
gill netting RFAI scores rated the forebay (RFAI=44) zone good and the transition (RFAI=36) fair.
Summary of Conditions in 1993 - Use Suitability
Fecal Coliform Bacteria—One informal swimming area and three boat ramps were each tested
for fecal coliform bacteria twelve times in 1993. No samples were collected within 48-hours of a rainfall of
at least one-half inch. Fecal coliform bacteria concentrations were very low (geometric mean concentration
<20/100 ml) at all four sites.
Fish Tissue—There are no fish consumption advisories on South Holston Reservoir. The most
recent TVA data for fish tissue samples are for fish collected in autumn 1991. The single composite of
channel catfish from the forebay had low or nondetectable concentrations of all pesticides, PCBs, and
metals (except mercury). The mercury concentration was 0.42 (ig/g, just high enough to be of interest.
Additional fish tissue samples were collected from the forebay in autumn 1993, but results were not
available at the time this report was prepared.
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Watauga Reservoir
Summary of Conditions in 1993 - Ecological Health
Water—The average flow through Watauga Reservoir in 1993 was near normal with an average
residence time of about 404 days. Watauga Reservoir was strongly stratified with a maximum temperature
difference in the forebay water column of 21.3°C in July. The maximum surface temperature was 28.8°C
at mid-reservoir in July, less than Tennessee's maximum temperature criterion for aquatic life of 30.5°C. At
the forebay, the area of DO depletion (DO < 2.0 mg/]) was limited to the bottom of the water column in
October. At mid-reservoir, areas of DO depletion developed in both the metalimnion and at the bottom of
the reservoir in September and October. The limited amount of DO depiction gave the forebay a rating of
good and mid-reservoir a rating of fair for DO in the reservoir ecological health index.
The maximum conductivity was 101 ^.mhos/cm at the forebay and 96 (imhos/cm at mid-reservoir,
both at the bottom of the water column in September. At both stations pH reached 9.0 near the surface, the
minimum pH was 6.5 in the mid-reservoir metalimnion in September.
Total nitrogen concentrations in April were 0.80 mg/1 at mid-reservoir and 0.61 mg/1 at the
forebay, about three-fourths of the total at each site as nitrates. The total nitrogen concentration in August
was about half the April total with the reduction due to a decline in nitrate concentrations as organic
nitrogen concentrations rose slightly. Total phosphorus concentrations in April were 0.02 mg/1 at mid-
reservoir and 0.01 mg/1 at the forebay. August concentrations were about half of the April total. TN/TP
ratios were 40 or higher for each sample Dissolved ortho phosphorus concentrations were at or below the
detection limit of 0.002 mg/1 for all four samples. Total organic carbon concentrations at mid-reservoir
were 1.8 and 3.2 mg/1 in April and August, respectively, and 2.1 mg/1 at the forebay in August.
The average chlorophyll a concentration was 4.1 (j.g/1 at the forebay and 5.9 fig/1 at mid-reservoir.
These concentrations are in the good range for the reservoir ecological health index. Secchi depths varied at
the forebay from 1.3 m in April to 3.9 m in May, and at mid-reservoir from 1.7 m in April to 4.2 m in
September.
Sediment—Chemical analyses of sediments in Watauga Reservoir in 1993 indicated the presence
of chlordane in both forebay (22 fig/kg) and in the mid-reservoir (36 ng/kg) Elevated levels of un-ionized
ammonia (260 |ig/l) were found in the forebay Toxicity tests detected acute toxicity to daphnids (0 percent
survival) and rotifers (5 percent survival) in the forebay. Particle size analysis showed sediments in the
forebay were about 100 percent silt and clay, and in the mid-reservoir were 99 percent silt and clay.
Sediment quality ratings used in the overall Watauga Reservoir ecological health evaluation for
1993 were poor at the forebay (acute toxicity to daphnids and rotifers and presence of chlordane and
ammonia); and good at the mid-reservoir site (presence of chlordane).
Benthic Macroinvertebrates—The first year that the bcnthic macroinvertebratc community was
evaluated on Watauga Reservoir was 1993. The forebay and mid-reservoir sites both had very poor benthic
•J
communities with only 7 and 9 taxa, respectively, and 158 and 60 organisms/m , respectively. The forebay
was dominated by Tubificidae (79 percent of the total) and the inflow was dominated by the chironomid
Einfeldia sp (53 percent).
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Scores at both sites were negatively influenced by three common factors: low diversity, the
absence of EPT taxa, and the absence of long-lived taxa. An interesting difference was observed between
the forebay and inflow sites on Watauga: the forebay site was overwhelmingly dominated by the tubificids
which negatively impacted the community rating, but very few chironomids were found, whereas the inflow
site was overwhelmingly dominated by chironomids which negatively impacted the rating at that site, but
very few tubificids were found.
Fish Assemblage—Combined fish samples in shoreline electrofishing (30 transects) and offshore
gill netting (24 net-nights) produced a total of 1,102 individuals including 20 species in the transition and
forebay zones of Watauga Reservoir. No sampling was conducted in the inflow zone. Fish were more
abundant in the transition zone (63 percent of total) but diversity was similar in both sample areas (14 taxa
in the forebay and 17 in the transition). The three dominant species by number were bluegill (23 percent),
gizzard shad (20 percent), and walleye (16 percent). Other common species were spotfin shiners
(11 percent), and rockbass (9 percent).
Analysis of shoreline electrofishing data identified a very poor littoral fish community in the
forebay zone (RFAI=20) of Watauga Reservoir. In fact, the forebay score of 20 was the lowest observed
(in both 1992 and 1993) in comparable areas of other tributary reservoirs that were sampled. The low
forebay RFAI resulted from minimum scores in eight of the twelve metrics used for evaluation. Although
the transition zone (RFAI=40) fish community rated only fair, it did receive maximum scores in five of the
twelve metrics. Gill netting RFAI evaluations rated the transition zone (RFAI=34) fair and forebay
(RFAI=30) poor. The slightly lower forebay rating resulted from minimum scores for six of the twelve
metrics.
Combined electrofishing and gill netting RFAI score of 25 indicated a poor rating for the forebay
(only Parksville Reservoir had a lower forebay score). The transition zone (RFAI=37) rated fair.
Summary of Conditions in 1993 - Use Suitability
Fecal Coliform Bacteria—The swimming beach at Shook Branch Recreation Area and an
informal swimming area at Watauga Point and three boat ramps were tested for fecal coliform bacteria
twelve times each in 1993. No sample was collected within 48-hours of a rainfall of one-half inch or
greater Fecal coliform bacteria concentrations were very low (geometric mean concentration <20/100 ml)
at all five sites.
Fish Tissue—There are no fish consumption advisories on Watauga Reservoir. The most recent
fish tissue collections by TVA were made in autumn 1991. All pesticides, PCBs, and metals (except
mercury) were low or not detected in the single channel catfish composite from the forebay. The mercury
concentration was 0.53 fig/g. Additional fish tissue screening samples were collected in autumn 1993, but
results were not available at the time this report was prepared.
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Holston River Stream Monitoring Site
Summary of 1993 Conditions - Ecological Health
Water—The water of the Holston River is moderately hard (average hardness of 113 mg/1) and
moderately alkaline (average total alkalinity of 94 mg/1). The median pH for the stream monitoring site was
8.0. The river was well oxygenated with dissolved oxygen levels ranging from 88 to 106 percent of
saturation.
Of the 12 streams monitored across the Tennessee Valley, the Holston River station ranked among
the highest in average nitrate+nitritc-nitrogen (0.67 mg/1) and just above the median for average total
phosphorus (0.112 mg/1), dissolved orthophosphate (0.057 mg/1), and ammonia nitrogen (0.038 mg/1). The
average concentration of organic nitrogen (0.185 mg/1) was among the lowest recorded. The high average
total phosphorus and average nitrate+nitrite-nitrogen concentrations yielded a poor rating for nutrients at
the site.
Seven analyses for priority pollutant metals (dissolved cadmium, lead, nickel, silver, and zinc and
total copper and zinc) were performed bi-monthly. Dissolved cadmium was detected in 4 of 6 samples.
Dissolved nickel was detected in 1 of 6 samples. Neither metal exceeded EPA criteria for protection of
aquatic life or human health.
Sediment—Sediment quality rated good in 1993 with no acute toxicity observed No PCBs or
pesticides exceeding the EPA guidelines. However, copper was detected at a level slightly above the EPA
guideline for copper in sediment. This was an improvement over 1992 when sediment quality rated fair.
Benthic Macromvertebrates—In 1993, benthic macroinvertebrates rated fair with a Modified
2
Benthic Index of Biotic Integrity (MBIBI) score of 36, with 59 taxa and 4,673 organisms/m . Conditions
2
in 1992 also rated fair (MBIBI score 41) with 50 taxa and 3,311 organisms/m . Dominant organisms in
1993 were dipteran midge larvae (30 percent), dipteran black-fly larvae (25 percent), and river snails
(10 percent). River snails were the most dominant group in 1992 (43 percent), followed by coleopteran
riffle beetles (10 percent) and caddisflies (7 percent). Siltation from agricultural land usage along the river
and pollution from industries located upstream have a major impact on benthic organisms at this site.
Fish Community Assessment—The fish community rated good with an Index of Biotic Integrity
(1BI) score of 48, improving from a rating of fair (IBI = 44) in 1992. Improvement was seen mainly in
decreased proportions of both tolerant fish and omnivorous fish suggesting some relief from chronic
nutrient enrichment of the river. Other problems for the fish community continued to be reflected by low
numbers of darter, sunfish, sucker, and other native species, and low proportions of piscivorous fish.
Adverse conditions observed were nutrient enrichment (evident in the abundance of aquatic vegetation), and
alteration of flow by releases from Fort Patrick Henry Dam.
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Summary of 1993 Conditions - Use Suitability
Fecal Cohform Bacteria—Seven sites on South Fork Holston River were tested twelve times each
for fecal coliform bacteria in 1993. No samples were collected within 48-hours of a rainfall of at least one-
half inch. Six sites were located between South Holston Dam and Boone Reservoir. Thomas and Beidleman
Creeks were sampled near their confluence with South Fork Holston River. The geometric mean
concentration of fecal coliforms on both streams were about 250/100 ml, a little higher than Tennessee's
water quality criterion for recreation of 200/100 ml. The other sites were on South Fork Holston River. The
two sites between the South Holston Weir and the confluence with Thomas Creek and the site downstream
of Thomas Creek but upstream of Beidleman Creek all had very low fecal coliform bacteria concentrations
(geometric mean <20/100 ml). The site downstream of Beidleman Creek had a geometric mean
concentration of 31/100 ml, and the site downstream of Boone Dam at Fordtown Bridge had a geometric
mean concentration of 52/100 ml Three sites on South Fork Holston River are boat launching sites.
Samples at the other sites were taken from the middle of the stream off a bridge, including a footbridge at
the most upstream site.
Fish Tissue—A five fish composite each of carp, channel catfish, and largemouth bass were
collected during summer 1992 and analyzed for selected metals, pesticides, and PCBs. All analytes were
not detected or found in low concentrations except slightly elevated levels of mercury in largemouth
(0.57 ng/g), PCBs in carp (0.6 (ig/g), and chlordane in channel catfish (0.08 (Jg/g).
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CONTENTS - VOLUME I
TABLES vi
FIGURES vi
EXECUTIVE SUMMARY viii
1.0 INTRODUCTION 1
1.1 Background 1
1.2 Objectives 1
1.3 Summary Report Description 2
2.0 DATA COLLECTION METHODS 5
2.1 Vital Signs Monitoring 5
2.1.1 Introduction 5
2.1.2 Reservoir Vital Signs Monitoring 7
Physical/Chemical Characteristics of Water 7
Acute Toxicity and Physical/Chemical Characteristics of Sediment 8
Benthic Macroinvertebrate Community Sampling 9
Fish Assemblage Sampling 10
Aquatic Macrophytes 11
2.1.3 Stream Vital Signs Monitoring 11
Physical/Chemical Characteristics of Water 12
Acute Toxicity and Physical/Chemical Characteristics of Sediment 13
Benthic Macroinvertebrate Community Sampling 13
Fish Community Sampling 14
2.2 Use Suitability Monitoring 14
2.2.1 Bacteriological Sampling 15
2.2.2 Fish Tissue Sampling 15
3.0 ECOLOGICAL HEALTH AND USE SUITABILITY DETERMINATION METHODS .... 29
3.1 Vital Signs Monitoring 29
3.1.1 Introduction 29
3.1.2 Reservoir Ecological Health 29
Dissolved Oxygen (DO) Rating Scheme 30
Chlorophyll Rating Scheme 32
Sediment Quality Rating Scheme 33
Benthic Community Rating Scheme 34
Fish Assemblage Rating Scheme 36
Overall Reservoir Health Determination 38
3.1.3 Stream Ecological Health 40
Nutrient Concentration Rating Scheme 41
Sediment Quality Rating Scheme 41
Benthic Community Rating Scheme 42
Fish Community 43
3.2 Use Suitability 44
3.2.1 Bacteriological Quality Evaluation 44
3.2.2 Fish Tissue Consumption Advisories 45
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4.0 HYDROLOGIC OVERVIEW OF 1993 59
4.1 Atmospheric Temperature 61
4.2 Rainfall 62
4.3 Streamflow 63
5.0 DISCUSSION 67
5.1 Vital Signs Monitoring 69
5.1.1 Reservoirs 69
Run-Of-The-River Reservoirs 69
Tributary Reservoirs 71
5.1.2 Streams 74
5.2 Use Suitability Monitoring 75
5.2.1 Bacteriological Studies 75
5.2.2 Fish Tissue Studies 76
Screening Studies 76
Intensive Studies 77
WATERSHED-BY-WATERSHED SUMMARY
6.0 KENTUCKY RESERVOIR WATERSHED 81
6.1 Kentucky Reservoir 83
6.2 Beech Reservoir 85
7.0 DUCK RIVER WATERSHED 87
7.1 Normandy Reservoir 89
7.2 Duck River Stream Monitoring Site 91
8.0 PICKWICK RESERVOIR - WILSON RESERVOIR WATERSHED 93
8.1 Pickwick Reservoir 95
8.2 Wilson Reservoir 97
8.3 Bear Creek Reservoir 99
8.4 Little Bear Creek Reservoir 101
8.5 Cedar Creek Reservoir 103
8.6 Bear Creek Stream Monitoring Site 105
9.0 WHEELER RESERVOIR - ELK RIVER WATERSHED 107
9.1 Wheeler Reservoir 109
9.2 Tims Ford Reservoir Ill
9.3 Elk River Stream Monitoring Site 113
10.0 GUNTERSVILLE RESERVOIR - SEQUATCHIE RIVER WATERSHED 115
10.1 Guntersville Reservoir 117
10.2 Sequatchie River Stream Monitoring Site 119
11.0 NICKAJACK RESERVOIR - CHICKAMAUGA RESERVOIR WATERSHED 121
11.1 Nickajack Reservoir 123
11.2 Chickamauga Reservoir 125
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12.0 HIWASSEE RIVER WATERSHED 127
12.1 Hiwassee Reservoir 129
12.2 Chatuge Reservoir 131
12.3 Nottely Reservoir 133
12.4 Blue Ridge Reservoir 135
12.5 Ocoee Reservoir No. 1 (Parksville Reservoir) 137
12.6 Hiwassee River Stream Monitoring Site 139
13.0 WATTS BAR RESERVOIR, FORT LOUDOUN RESERVOIR,
AND MELTON HILL RESERVOIR WATERSHED 141
13.1 Watts Bar Reservoir 143
13.2 Fort Loudoun Reservoir 145
13.3 Melton Hill Reservoir 149
13.4 Emory River Stream Monitoring Site 151
14.0 CLINCH RIVER AND POWELL RIVER WATERSHED 153
14.1 Norris Reservoir 155
14.2 Clinch River Stream Monitoring Site 157
14.3 Powell River Stream Monitoring Site 159
15.0 LITTLE TENNESSEE RIVER WATERSHED 161
15.1 Tellico Reservoir 163
15.2 Fontana Reservoir 165
15.3 Little Tennessee River Stream Monitoring Site 167
16.0 FRENCH BROAD RIVER WATERSHED 169
16.1 Douglas Reservoir 171
16.2 French Broad River Stream Monitoring Site 173
16.3 Nolichucky River Stream Monitoring Site 175
17.0 HOLSTON RIVER WATERSHED 177
17.1 Cherokee Reservoir 179
17.2 Fort Patrick Henry Reservoir 181
17.3 Boone Reservoir 183
17.4 South Holston Reservoir 185
17.5 Watauga Reservoir 187
17.6 Holston River Stream Monitoring Site 189
REFERENCES 191
CONTENTS FOR VOLUME II 197
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.0
4
1012402
KEY CONTACTS FOR MONITORING FUNCTIONS
Monitoring Program Design
Neil Carriker
Don Dycus
(615) 751-7330
(615) 751-7322
Water Quality Monitoring
Physical/Chemical
Reservoirs
Streams
Bacteriological
Dennis Meinert
Jan Strunk
Joe Fehring
(615) 751-8962
(615) 751-8637
(615) 751-7308
Sediment Quality
Physical/Chemical
Toxicity
Dennis Meinert
Damien Simbeck
(615) 751-8962
(205) 729-4549
Biological Monitoring
Fish
Ecology
Reservoirs
Streams
Consumption
Benthic Macroinvertebrates
Reservoirs
Streams
Ecological Health
Gary Hickman
Charlie Saylor
Don Dycus
Amy Wales
Steve Ahlstedt
Don Dycus
Dennis Meinert
(615) 632-1791
(615) 632-1779
(615) 751-7322
(615) 751-7831
(615) 632-1781
(615) 751-7322
(615) 751-8962
date due
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