&EPA
United States
Environmental Protection
Agency
Environmental Research
Laboratory
Duluth MN 55804
EPA-600/3-80-005
January 1980
Research and Development
Acute Toxicity of
Toxaphene to
Fathead Minnows,
Channel Catfish, and
Bluegills
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RESEARCH REPORTING SERIES
Research reports of the Office of Research and Development, U S Environmental
Protection Agency, nave been grouped into nine series These nine broad cate-
gories were established to facilitate further development and application of en-
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This document is available to the public through the National Technical Informa-
tion Service, Springfield, Virginia 22161.
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EPA-600/3-80-005
January 1980
ACUTE TOXICITY OF TOXAPHENE TO FATHEAD MINNOWS,
CHANNEL CATFISH, AND BLUEGILLS
by
W. Waynon Johnson
Arnold M. Julin
U.S. Fish and Wildlife Service
Fish-Pesticide Research Laboratory
Columbia, Missouri 65201
Contract No. EPA-IAG-141(D)
Project Officer
Leonard H. Mueller
Environmental Research Laboratory
Duluth, Minnesota 55804
ENVIRONMENTAL RESEARCH LABORATORY
OFFICE OF RESEARCH AND DEVELOPMENT
U. S. ENVIRONMENTAL PROTECTION AGENCY
DULUTH, MINNESOTA 55804
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DISCLAIMER
This report has been reviewed by the Environmental Research Laboratory -
Duluth, U.S. Environmental Protection Agency, and approved for publication.
Approval does not signify that the contents necessarily reflect the views and
policies of the U.S. Environmental Protection Agency, nor does mention of
trade names or commercial products constitute endorcement or recommendation
for use.
ii
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FOREWORD
This report describes the toxicity of toxaphene, a widely used
insecticide, to three species of fish, fathead minnows, channel catfish,
and bluegills. Research compared the acute toxicity of static tests with
continuous flow exposure. Also studied was the importance of various life
stages of aquatic organisms when exposed to a chemical pollutant. Environ-
mental variables, pH, water hardness, and temperature were studied under
laboratory test conditions to determine their effects on toxaphene toxicity.
J. David Yount, Ph.D.
Deputy Director
Environmental Research Laboratory-Duluth
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ABSTRACT
Toxaphene was very toxic to fathead minnows (Pimephales promelas), chan-
nel catfish (Ictalurus punctatus), and bluegills (Lepomis macrochirus) in
static tests; 96-h LCSO's ranged from 2.6 to 20 ug/1 at 20~. Fathead min-
nows were the least susceptible and bluegill and channel catfish were about
equal in susceptibility. Prolonged exposures of 12 to 34 days in flow-through
tests produced time-independent LC50 values of 0.6 to 1.9 ug/1, significantly
lower than the 96-h values.
The toxicity of toxaphene was not influenced by variations in pH or water
hardness in static tests. Temperature seemed to influence rate of onset
rather than degree of response. Toxicities were similar at 20 and 25 C in
flow-through tests, however, a decrease in the time required for mortality to
become asymptotic with time was observed. Time-independence was reached af-
ter 7 to 16 days of exposure at 25 C while 24 to 34 days were required at
20 C.
The life stage of channel catfish most sensitive to toxaphene poisoning
was the swim-up fry with a 96-h LC50 of 0.8 ug/1. Early yolk sac fry were
extremely resistant with a 24-h LC50 of 4.7 mg/1 however, within 96 hours the
yolk had absorbed and the LC50 had declined to 8.0 ug/1.
This report was submitted in partial fulfillment of Contract No. EPA-IAG-
141(D) by the Fish-Pesticide Research Laboratory under the sponsorship of the
U.S. Environmental Protection Agency. This work was completed as of April,
1976.
iv
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CONTENTS
Foreword iii
Abstract iv
Tables vi
Figures vi
Acknowledgments vii
1. Introduction 1
2. Conclusions 2
3. Recommendations 3
4. Methods and Materials 4
5. Results 6
6. Discussion 14
References 17
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TABLES
Number
Acute toxicity of toxaphene to three fishes at two
temperatures in static toxicity tests 7
Acute toxicity of toxaphene to three fishes at two
temperatures in flow-through toxicity tests 8
Influence of temperature, pH, and water hardness on the
acute toxicity of toxaphene to fingerling channel catfish
in static tests 9
The acute toxicity of toxaphene to three life stages of
channel catfish in static tests at 25 C 10
vi
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FIGURES
Number Page
1 Response curve for fathead minnows exposed to toxaphene in
flow-through toxicity tests 11
2 Response curve for channel catfish exposed to toxaphene in
flow-through toxicity tests 12
3 Response curve for bluegills exposed to toxaphene in flow-
through toxicity tee«s 13
vii
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ACKNOWLEDGMENT
We thank Donnie W. Short for assisting us in performing the static
toxicity tests and Michael J. Nevins for performing the flow-through toxicity
tests. Special appreciation is expressed to Mr. Nevins for performing all
of the LC50 calculations.
viii
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SECTION 1
INTRODUCTION
Within recent years a general concern has developed among scientists
about the use of persistent pesticides that are becoming more abundant and
widespread in the environment. This concern has induced an increased aware-
ness and closer scrutiny of the effects these chemicals may impose on organ-
isms in the aquatic environment. As more chemicals face either registration
cancellation or increased restrictions on their use, pesticide users are
forced to depend more and more on fewer alternative chemicals. As a conse-
quence, these chemicals are receiving greater attention from researchers and
many are being found to produce detrimental environmental effects.
One compound, toxaphene, has replaced many of the agricultural applica-
tions of DDT, for which registration has been canceled. This use has result-
ed in an increased environmental distribution of toxaphene, and it has been
identified as a residue in water and aquatic organisms in various studies
(1-4). Toxaphene, like many of the organochlorine chemicals, is persistent
(5-9) and highly toxic to fish and other aquatic organisms (10-16). Because
of its toxicity to fish, toxaphene was proposed and used as a fish eradicant
(17-23). However, the treated waters often remained highly toxic throughout
a detoxification time of a few weeks to several years (7, 8, 24-26). This
slow detoxification rate led to the eventual elimination of toxaphene as a
piscicide, but only after a number of lakes were contaminated with its
residues.
Recent data from the National Pesticide Monitoring Program indicate that
toxaphene is becoming a more common pollutant in the aquatic environment
(D. Walsh, personal communication), thereby increasing the likelihood of its
occurrence in diverse habitats and during different stages of a fish's life
cycle. The literature contains few data on the effects of environmental
variables on toxaphene toxicity or on the susceptibility of different life
stages(10). We therefore undertook the present study with the following
objectives: (1) to compare the susceptibilities of bluegills, channel cat-
fish, and fathead minnows to toxaphene; (2) to compare the toxicity of
toxaphene to these species under static and flow-through test conditions; (3)
to determine the effects of temperature, pH, and water hardness on the
toxicity of toxaphene to channel catfish; and (4) to compare the susceptibil-
ities of different life stages of channel catfish to toxaphene.
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SECTION 2
CONCLUSIONS
Toxaphene is highly toxic to fingerling bluegills, channel catfish, and
fathead minnows in static toxicity tests,'as evidenced by 96-h LCSO's ranging
from 2.6 to 20 ug/1 at 20 C and from 2.4 to 23 ug/1 at 25 C.
Time-independent LC50 values (indicating the concentrations where mortal-
ity becomes asymptotic with time) for all three species were in the range of
0.6 to 1.9 ug/1.
Water hardness and pH did not appreciably alter toxaphene toxicity.
Temperature appeared to hasten the rate of onset but not the degree of
response. For an equivalent response fish required a longer time at 20 C
than at 25 C.
In channel catfish, early swim-up fry were the most susceptible life
stage (96-h LC50, 0.8 ug/1); yolk-sac fry, before yolk absorption, were the
least susceptible (24-h LC50, 4.7 mg/1).
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SECTION 3
RECOMMENDATIONS
The 96-h LC50 should be used in preference to the lethal threshold con-
centration when calculating application factors or maximum acceptable toxicant
concentrations.
Thorough studies of the acute toxicity of toxicants to different life
stages of fish species and the influence on toxicity by environmental variables
such as temperature, pH, and hardness should be performed when "safe" levels
of pollutants are being estimated from acute toxicity data.
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SECTION 4
METHODS AND MATERIALS
Channel catfish (Ictalurus punctatus), and bluegllls (Lepomis macrochirus)
used in the toxicity tests were obtained from National fish hatcheries as
fingerlings (weight range, 0.5 to 1.5 g). Fathead minnows (Pimephales
promelas) were reared in ponds from stock obtained from the Environmental
Research Laboratory, Duluth, Minnesota. Although the minnows were in the
same size range, they were immature adults rather than fingerlings. Early
life stages of channel catfish were reared from eggs produced at the Fish-
Pesticide Research Laboratory. Fish used in any single test were of the same
lot and were held in laboratory facilities similar to those described by
Brauhn and Schoettger (27) for at least 14 days before testing. Holding
facilities were supplied with 17 C well water with a pH of 7.4 and alkalinity
and total hardness of 237 and 272 mg/i (as CaCO.,), respectively. Channel cat-
fish eggs were hatched and the fry reared at 25 C.
Toxicity tests were conducted according to the procedures outlined in
American Public Health Association (28) and Committee for Methods for Toxicity
Tests with Aquatic Organisms (29). Basic static tests were conducted in re-
constituted water with a pH of 7.4 and alkalinity and total hardness of 35 and
40 mg/1 (CaCO ), respectively. The influence of water quality was investigat-
ed by measuring toxicity at various pH's and water hardnesses. Appropriate
buffers and salt mixtures were used to attain the desired values while main-
taining other variables constant (29, 30). Water quality values were measured
prior to each test to assure that they were within the recommended range of
values. Tests were conducted at temperatures of 15, 20, and 25 C and main-
tained (+ 1 C) by constant temperature water baths. Flow-through tests were
conducted in the well water described above using a proportional diluter
system modeled after Mount and Brungs (31) and modified as recommended by
McAllister et al. (32). The dilution ratio between test concentrations was
0.75. Well water used in the flow-through tests was first passed through an
ultraviolet light sterilizer. Ten fish per concentration were used in static
tests and 30 per concentration in flow-through tests; at least 8 concen-
trations were used in each test.
Technical toxaphene used in this study was supplied by Hercules, Incorpo-
rated, Wilmington, Delaware. It is described as being chlorinated camphene
containing 67 to 69% chlorine and is considered to be 100% active ingredient
(33). Stock solutions were prepared by dissolving the required amount of
chemical in acetone. Test concentrations were accomplished by the addition of
an appropriate amount of the stock solution to a test vessel. Amounts of
acetone to water were 1 ml/1 or less. All concentrations were based on the
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total amount of chemical used and all data are expressed as concentrations of
total material. In flow-through tests, concentrations delivered to each test
vessel were determined by dye calibration of the diluter system. All concen-
trations are expressed as nominal rather than measured values.
Toxicity values are expressed as LC50's (estimated concentration lethal
to 50% of the test population) and were calculated according to the log-
probit method of Litchfield and Wilcoxon (34). Values were considered
significantly different when the 95% confidence limits about the LCSO's did
not overlap (28). If less than 50% of the organisms died in the highest con-
centration, the LC50 for that test was stated as being greater than that con-
centration. Time-independent lethal concentrations (TILCSO-concentration
estimate at which 50% of the test population can survive for an indefinite
period of exposure) were calculated by the method of Green (35). For these
determinations, except for the bluegill test at 25 C, exposures were con-
tinued for 30 days or until total mortality over a 4 day period was 5% or less
of the test population and the daily mortality in any single concentration
did not exceed 10% of the initial number of animals per concentration.
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SECTION 5
RESULTS
Static toxiclty tests showed that fathead minnows were the least sensi-
tive to toxaphene and bluegills and channel catfish were about equal in
susceptibility (Table 1). The 96-h LC50 of 20 ug/1 for fathead minnows at
20 C was 7.7 times the value for bluegills and 4.8 times that for channel cat-
fish. The greater resistance of the fathead minnows, however, may have been
a consequence of the difference in maturity between them and the bluegills
or channel catfish. An increase in test temperature from 20 to 25 C did not
appear to alter the toxicity for any of the three species.
After continuous exposure in flow-through tests at 20 C, the 96-h LC50
of 7.0 ug/1 observed for fathead minnows was about one-third that observed
in static tests (Table 2). Such a large within species difference was not
apparent between the two test methods in bluegills or channel catfish. When
exposures were continued until response became asymptotic with time, LC50
values decreased to one-half or less of the 96-h values; the estimated
TILCSO's were 0.6 ug/1 for bluegills, 1.0 ug/1 for channel catfish, and 1.8
ug/1 for fathead minnows.
Although differences in response were observed, the changes in LCSO's
that occurred in flow-through tests when temperatures were increased from 20
to 25 C were irregular and relatively small. It was noted, however (except
in the test with bluegills where system failure forced early termination of
the test), that the tests at 25 C reached time-independence in response at an
earlier date (7 to 16 days) than those at 20 C (24 to 34 days) (Figs. 1-3).
Even so, the TILCSO's for all species and temperatures tested were similar.
The lethality of toxaphene to channel catfish did not appear to be al-
tered by pH, water hardness, or temperature in static tests (Table 3). The
96-h LCSO's were not materially changed when temperatures varied from 15 to
25 C, pH from 6.5 to 8.3, or total hardness from 10 to 320 ug/1 (CaCO_). An
exception was the 24-h LC50 of 12.5 ug/1 at 15 C, which was considerably
higher than the values at 20 and 25 C.
A substantial difference in susceptibility was observed between early
life stages of channel catfish. Newly hatched fry, before absorption of the
yolk, were extremely resistant to toxaphene poisoning as indicated by the
24-h LC50 of 4700 ug/1 (Table 4). However, the toxicity sharply increased as
the yolk was observed. After 96 hours, when all yolk had been absorbed, the
LC50 decreased to 8.0 ug/1. This increase in susceptibility continued to the
swim-up fry stage where LCSO's were 4.0 ug/1 at 24 hours and 0.8 at 96 hours.
Thereafter, resistance increased; the swim-up fry were the most sensitive life
stage.
6
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TABLE 1. ACUTE TOXICITY OF TOXAPHENE TO THREE FISHES AT TWO TEMPERATURES IN
STATIC TOXICITY TESTS.
(ug/1)
*a
Species
Fathead minnow
Channel catfish
Bluegill
20 C
24 h
24
(20-28)
7.8
(6.3-9.6)
6.8
(6.2-7.4)
96 h
20
(15-27)
4.2
(2.9-6.0)
2.6
(2.2-3.0)
25 C
24 h
23
(18-29)
6.4
(4.9-8.4)
6.6
(5.5-7.4)
96 h
23
(18-29)
3.7
(2.3-6.0)
2.4
(2.1-2.7)
size ranged from 0.5 to 1.5 g.
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oo
TABLE 2. ACUTE TOXICITY OF TOXAPHENE TO THREE FISHES AT TWO TEMPERATURES IN FLOW-THROUGH TOXICITY
TESTS.
(ug/1)
LC50 values (and 95% confidence limits)
Species
Fathead
minnow
Channel
catfish
Bluegill
Temp 4
(OG) days
20 7.0
(6.3-7.
25 5.0
(3.4-7.
20 5.5
(4.9-6.
25 7.5
(6.0-9.
20 4.7
(4.4-5.
25 3.4
(3.0-3.
8
days
4.3
7) (3. 8-4.
2.1
4) (1.5-3.
4.4
2) (4. 0-4.
3.7
4) (3. 0-4.
2.1
0) (1.9-2.
8)
12
days
3.6
9X3.3-3
1.8
0) (1.3-2
3.2
9) (2. 9-3
3.7
5) (3. 0-4
1.4
3) (1.3-1
16
days
2.9
,9)(2. 7-3.1)
1.5
.3) (1.0-2.1)
2.9
.5X2.6-3.2)
.5)
1.2b
.5)
20 24
days days
2.7 2.6
(2.5-2.9X2.5-2.7)
2.5 2.1
(2. 2-2. 8) (1.9-2. 3)
0.9b 0.8
(0.6-0.8)
Terminal
Day
24
(2
16
(1
29
(1
12
(3
34
7
(1
value
LC50
2.6
.5-2.7)
1.5
.0-2.1)
1.9
.7-2.1)
3.7
.0-4.5)
0.7
1.4
.2-1.7)
TILC50
1.8
1.0
1.0
1.9
0.6
size ranged from 0.5 to 1.5 g except for channel catfish which were 4 g in the 20 C test and
O.lSgin the 25 C test.
Data inadequate to calculate confidence limits.
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TABLE 3. INFLUENCE OF TEMPERATURE, pH, AND WATER HARDNESS ON THE
ACUTE TOXICITY OF TOXAPHENE TO FINGERLING CHANNEL CATFISH3
IN STATIC TESTS.
(ug/1)
Test Conditions
Temp
(°C) PH
15 7.4
20 7.4
25 7.4
20 6.5
20 7.5
20 8.3
20 8.2
20 8.2
20 8.2
20 8.2
Alkalinity
(mg/1)
35
35
35
35
35
35
220
220
220
220
Hardness
(mg/1)
40
40
40
40
40
40
10
40
160
320
LC50 values (and
95% confidence limits)
24 h
12.5
(9.7-16.1)
7.8
(6.3-9.6)
6.4
(4.9-8.4)
6.2
(3.9-10.0)
7.9
(5.9-10.5)
7.5
(6.3-9.0)
5.6
(4.2-7.5)
6.7
(5.2-8.6)
6.1
(4.6-8.0)
7.3
(5.8-9.3)
96 h
4.7
(3.2-6.8)
4.2
(2.9-6.0)
3.7
(2.3-6.0)
2.7
(1.9-3.8)
3.4
(2.5-4.6)
3.0
(2.1-4.3)
3.9
(3.1-4.8)
3.2
(2.3-4.4)
3.9
(2.0-5.1)
4.7
(3.7-5.9)
SFlsh size ranged from 0.5 to 1.5 g.
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TABLE 4. THE ACUTE TOXICITY OF TOXAPHENE TO THREE LIFE STAGES OF
CHANNEL CATFISH IN STATIC TESTS AT 25 C.
(ug/1)
a
LC50 values (and
95% confidence limits)
Life stage 24 h 96 h
Yolk-sac fry 4700 8.0
(3040-7260) (6.0-10.6)
Swim-up Fry 4.0 0.8
(3.2-5.0) (0.5-1.2)
Fingerling 7.0 2.8
(5.4-9.1) (2.0-4.0)
^oik-sac fry were 1 to 4 days old, swim-up fry were 5 to 8 days old,
and fingerlings size ranged from 0.5 to 1.5 g.
10
-------
10-
LC50
4-
2-
= 20 C
= 25 C
o—o
r
8
12
—T-
16
—i—
20
24
Days
Figure 1. Response curve for fathead minnows exposed to toxaphene in
flow-through toxicity tests.
-------
ro
iu-
8-
LC50 fi
(MO/D
4-
2-
o = 20C
• =25C
0\
\ •
\\
O
-------
LC50
8-
6-
4-
o=20C
.= 25 C
-o—o.
o - o
0 - 0.
8 12 16 20 24 28 32
Days
36
Figure 3. Response curve for bluegills exposed to toxaphene in
flow-through toxicity tests.
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SECTION 6
DISCUSSION
Toxaphene, one of the more toxic of the organochlorine insecticides to
fish (12), has a lethal range of concentrations reported to be between 5 and
100 ug/1 for most freshwater species (36). Data on similar species from the
Fish-Pesticide Research Laboratory (37) show a range of 96-h LCSO's from
static toxicity tests of 2 to 23 ug/1, the upper limit for lethality being
lower than previously reported. Such differences in LC50 values, however,
could be due to variations in test methods and precision rather than to
toxicity limits. Data from the present study are in general agreement with
ranges reported for bluegills, channel catfish, and fathead minnows (38).
In comparison with the static tests, exposure of bluegills and channel
catfish to toxaphene in flow-through test systems did not produce an ap-
preciable increase in toxicity. In contrast, fathead minnows were notably
more susceptible to toxaphene poisoning in the flow-through system, thereby
eliminating the differences in susceptibility observed in static tests; in
effect, LCSO's were similar for all three species. The similarity in response
was maintained throughout the prolonged exposures and the terminal values
were all within the range of 0.7 to 3.7 ug/1.
Time-independent LCSO's were similar for all three species, although the
rate at which response became asymptotic with time varied considerably.
TILC50 values are of interest because they represent the theoretical concen-
tration at which 50% of the test population can survive toxicant exposure
for a prolonged period (39). Presumably, the surviving animals are suffi-
ciently able to handle these concentrations of chemical, through detoxifica-
tion, metabolism, or other means, to the extent that the imposition of mortal-
ity on the test population due to the toxicant exposure is no longer signif-
icant. In this context, the toxicant concentration should represent the
range where the response is no longer acute and becomes chronic in nature.
It has been suggested by Eaton (40) that the lethal threshold concen-
tration (LTC) is the more appropriate value to use in the calculation of ap-
plication factors as defined by Mount (41). He stated that it provides bet-
ter acute values to use with experimentally determined application factors
when computing "maximum acceptable toxicant concentrations" (MATC) for spe-
cies for which only acute toxicity data are available. He identified the LTC
value as the point in an acute toxicity test at which the mortality rate is
10% or less of the original number of fish in any concentration during the
preceeding 24 hours. Using this criterion, LTC values determined for our
(20 C) tests were 4.3, 4.5, and 2.0 ug/1 for fathead minnows, channel catfish,
14
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and bluegills, respectively. When compared with the 4 day LCSO's (Table 2),
the values are not greatly different for these species and would produce re-
latively small differences in calculated MATC values. If the definition of
an application factor presented by the National Academy of Sciences (38) is
used (the numerical value for the ratio of the safe concentration to the
acutely lethal concentration), it would seem that the 96-h LC50 would be as
acceptable as the LTC. Since, as a general rule, 96-h LCSO's would be less
expensive and time consuming to generate and there are broadly accepted,
standardized procedures for conducting 96-h toxicity tests (29), we recom-
mend the continued use of the 96-h LC50 for calculating MATC values when
experimentally determined values are not available. This would maintain
continuity with the National Academy of Sciences (38) since it uses the 96-h
LC50 in generating calculated MATC values.
If the arbitrary value of 0.01 is used as the application factor for
toxaphene (38), then the calculated values of the MATC's for bluegills,
channel catfish, and fathead minnows are 47, 55, and 70 ng/1, respectively.
From a chronic toxicity study with brook trout (Salvelinus fontinalis), Mayer
et al. (42) reports that the MATC is below 39 ng/1 and recommended that the
water concentration of toxaphene be below this value to protect this species.
Our data, however, indicate that this concentration may be adequate for the
protection of these three species.
Of the environmental variables studied, only temperature effected the
acute toxicity of toxaphene. Considering the chemical stability of toxaphene,
it would be expected that pH and water hardness, under laboratory test con-
ditions, would have little effects on toxicity. Although irregular in na-
ture, it appeared that higher temperatures increased the rate at which the
response occurred and a decrease in the time required for mortality to be-
come asymptotic with time was observed in the flow-through tests conducted
at 25 C. Such an influence on response time has previously been reported by
Hussein et al. (43) and Kopp (13). An explanation of these results is not
immediately apparent. Macek et al. (44) have suggested that rates of uptake
and enzyme activity may offer at least partial explanations of these data.
Variations in the susceptibility of different life stages appeared to be
a factor of major importance. Although the early yolk-sac fry were highly
resistant to toxaphene poisoning, susceptibility sharply increased after the
yolk was absorbed. We believe that the resistance of the yolk-sac fry may be
correlated with the lipid-solubility of toxaphene and that the yolk is a
reservoir in which toxaphene is sequestered. Data reported by Mayer et al.
(42), which indicated that brook trout fry accumulated toxaphene up to 76,000
times the water concentration within 15 days after hatching, appear to sup-
port this view. As yolk absorption advanced, toxaphene residues would be
mobilized and mortality would increase.
It was not surprising that swim-up fry were the most sensitive stage
studied. They were in the phase where feeding and movement were being in-
itiated and embryonic differentiation was being completed. It would be ex-
pected that an organism undergoing the stress of such physiological change
would be highly susceptible to externally superimposed stress. Significantly,
our data show that the 96-h LC50 for swim-up fry is equivalent to the as-
15
-------
ymptotic LC50 for fingerlings. Such data point out the importance of
studying various life stages of aquatic organisms as well as various species
when "safe" concentrations of pollutants are being determined.
16
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Grissinger, and P.A. Parsons. Pesticides in Water - Pesticide Residues in
Sediments of the Lower Mississippi River and its Tributaries. Pestic.
Monit. J. .3(1)58-66. 1959.
2. Ginn, T.M., and P.M. Fisher, Jr. Studies on the Distribution and Flux of
Pesticides in Waterways Associated with a Ricefield-Marsh-Land Ecosystem.
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Flora Before, During, and After Dredging Toxaphene-Contaminated Sediments.
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Persistence of Toxaphene in Lake Water and Its Uptake by Aquatic Plants
and Animals. J. Agric. Food Chem. 14(1):66-69. 1966.
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Sediments. Environ. Sci. Technol. 5.(3):230-234. 1971.
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Insecticides to Fish. Sewage Ind. Wastes 25_(7): 840-844. 1953.
17
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12. Henderson, C., Q.H. Pickering, and C.M. Tarzwell. Relative Toxicities of
Ten Chlorinated Hydrocarbons to Four Species of Fish. Trans. Am. Fish.
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13. Koppe, R. Bin Beitrag zur Toxikologie des Toxaphens gegenuber Fischer
und deren Nahrtieren owie die Wirkung bereits durch Toxaphen begifteten
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Respect to Fish and Aquatic Food Animals). Z. Fisch. Hilfswiss.
2:771-794. 1961.
14. Needham, R.G. Effects of Toxaphene on Plankton and Aquatic Invertebrates
in North Dakota Lakes. U.S. Bureau Sport Fisheries and Wildlife,
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Rev. Biol. Res. 10:5-7. 1958. ~
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91(l):14-22. 1962.
18
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26. Mayhew, J. The Use of Toxaphene as a Fish Poison in Strip Mine Ponds
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19
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39. Brown, V.M. Concepts and Outlook in Testing the Toxicity of Substances
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20
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TECHNICAL REPORT DATA
(Please read Instructions on the reverse before completing)
1. REPORT NO.
EPA-6QO/3-80-005
3. RECIPIENT'S ACCESSION NO.
4. TITLE AND SUBTITLE
Acute Toxicity of Toxaphene to Fathead Minnows,
Channel Catfish, and Bluegills
5. REPORT DATE
January 1980 issuing date
6. PERFORMING ORGANIZATION CODE
7. AUTHOR(S)
W. Waynon Johnson and Arnold M. Julin
8. PERFORMING ORGANIZATION REPORT NO.
9. PERFORMING ORGANIZATION NAME AND ADDRESS
U.S. Fish and Wildlife Service
Fish-Pesticide Research Laboratory
Columbia, Missouri 65201
10. PROGRAM ELEMENT NO.
1BA021
11. CONTRACT/GRANT NO.
EPA-IAG-141(D)
12. SPONSORING AGENCY NAME AND ADDRESS
Environmental Research Laboratory - Duluth, MN
Office of Research and Development
U.S. Environmental Protection Agency
Duluth, Minnesota 55804
13. TYPE OF REPORT AND PERIOD COVERED
14. SPONSORING AGENCY CODE
EPA/600/03
15. SUPPLEMENTARY NOTES
16. ABSTRACT
Toxaphene was very toxic to fathead minnows (Pimephales promelas), channel
catfish (Ictalurus punctatus), and bluegills (Lepomis macrochirus) in static tests;
96-h LCSO's ranged from 2.6 to 20 ug/1 at 20 C. Fathead minnows were the least
susceptible and bluegill and channel catfish were about equal in susceptibility.
Prolonged exposures of 12 to 34 days in flow-through tests produced time-independent
LC50 values of 0.6 to 1.9 ug/1, significantly lower than the 96-h values.
The toxicity of toxaphene was not influenced by variations in pH or water hardness
in static tests. Temperature seemed to influence rate of onset rather than degree of
response. Toxicities were similar at 20 and 25 C in flow-through tests, however, a
decrease in the time required for mortality to become asymptotic with time was
observed. Time-independence was reached after 7 to 16 days of exposure at 25 C while
24 to 34 days were required at 20 C.
The life stage of channel catfish most sensitive to toxaphene poisoning was the
swim-up fry with a 96-h LC50 of 0.8 ug/1. Early yolk sac fry were extremely
resistant with a 24-h LC50 of 4.7 mg/1, however, within 96 hours the yolk had adsorbed
and the LC50 had declined to 8.0 ug/1.
17.
KEY WORDS AND DOCUMENT ANALYSIS
a.
DESCRIPTORS
b.lDENTIFIERS/OPEN ENDED TERMS
COS AT I Field/Group
Pesticides
Bioassay
Fishes
Mortality
Toxaphene
Fathead minnows
Channel catfish
Bluegills
Acute toxicity
06 T,F
18. DISTRIBUTION STATEMENT
Release to Public
19. SECURITY CLASS (This Report}
Unclassified
21. NO. OF PAGES
29
20. SECURITY CLASS (Thispage)
Unclassified
22. PRICE
EPA Form 2220-1 (R«v. 4-77) PREVIOUS EDITION is OBSOLETE 01
JUS GOVERNMENT MINTING OFFICE: I9M -657-146/5541
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