vvEPA
United States
Environmental Protection
Agency
Office of Water
Regulations and Standards
Criteria and Standards Division
Washington DC 20460
EPA 440/5-86-006
September 1986
Water
Ambient
Water Quality
Criteria
for
Toxaphene -1986
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AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR
TOXAPHENE
U S. ENVIRONMENTAL PROTECTION AGENCY
OFFICE OF RESEARCH AND DEVELOPMENT
ENVIRONMENTAL RESEARCH LABORATORIES
DULUTH, MINNESOTA
NARRAGANSETT, RHODE ISLAND
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NOTICES
This document has been reviewed by the Criteria and Standards Division,
Office of Water Regulations and Standards, U.S. Environmental Protection
Agency, and approved for publication.
Mention of trade names or commercial products does not constitutes
endorsement or recommendation for use.
This document is available to the public through the National Technical
Information Service (NTIS), 5285 Port Royal Road, Springfield, VA 22161.
11
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FOREWORD
Section 304(a)(l) of the
Section r;J £ che Environmental frocecuiuu «6—, -
requires the Administrator or cne 3(,raraCelv re£lect the latest
publish water quality criteria that• a««£e£ aU identLfiable effects
scientific knowledge on the kind and «^ent ° ^ presence of pollutants
on health and welfare that might be«pecc document is a revision
in any body of water, incuding ground water. ^.^ ^
The t.M ".ace, ,u.y (H.
Clean Water Act, section 304Ca)U) and se.t oa 303 U) (2)
different program impact in each "«""; ^.^t of ecological etfects.
- ««n'« "" ""
. o
tepresents a non-regulatory, ««n'^« "" ""entific assessments. If
criteria presented in 'hi. doc«« «. .-ch . = »« ^ are adopted
vater quality criteria associated vitn sp become
by a state as »ater ^"^^^^jr.U^ion.'l. ambient water
"
by a state as »ater ^"^.ion.'l. ambient waters
hat State S.t«"ui!i^ criteria adopted in State water ,u.Uty
that btate. wansi H • ,, ,rai,lfJ<= aq criteria developed
become regulatory.
=r
William A. Whittington
Director
Office of Water Regulations and Standards
111
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ACKNOWLEDGMENTS
John G. Eaton
(freshwater author)
Environmental Research Laboratory
Duluth, Minnesota
Jeffrey L. Hyland
Robert S. Carr
(saltwater authors)
Battelle New England Laboratory
Duxbury, Massachusetts
Charles E. St;ephan
(document coordinator)
Environmental Research Laboratory
Duluth, Minnesota
David J. Hansen
(saltwater coordinator)
Environmental Research Laboratory
Narragansett, Rhode Island
Clerical Support: Shelley A. Heintz
Terry L. Highland
Nancy J. Jordan
Diane L. Spehar
Delcena R. Nisius
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CONTENTS
Page
111
Foreword
iv
Acknowledgments
vi
Tables
1
Introduction
Acute Toxicity to Aquatic Animals
. . 11
Chronic Toxicity to Aquatic Animals
.... 13
Toxicity to Aquatic Plants
13
Bioaccumulation
18
Other Data
20
Unused Data
22
Summary
23
National Criteria
59
References
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TABLES
Page
1. Acute Toxicity of Toxaphene to Aquatic Animals 25
2. Chronic Toxicity of Toxaphene To Aquatic Animals 37
3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic
39
Ratios
4. Toxicity of Toxaphene to Aquatic Plants 44
5. Bioaccumulation of Toxaphene by Aquatic Organisms 45
6. Other Data on Effects of Toxaphene on Aquatic Organisms 49
VI
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Introduction^
Toxaphene first became commercially available in 1948 under the trade
name "Hercules 3956" and has been used in various forms, such as emulsifiable
concentrates, wettable powders, dusts, and granular baits. Toxaphene is
produced by the chlorination of camphene, resulting in a mixture of at
least 175 separate components, mostly polychlorinated camphenes and bornanes,
with an average chlorine content of 67 to 69% (Casida et al. 1974; Holmstead
et al. 1974; Pollock and Kilgore 1978). The technical-grade product is an
amber, waxy solid with a vapor pressure of 0.17 to 0.4 mm Hg at 25°C, a
melting point range of 65 to 90'C, and a mild terpene odor. Its average
empirical formula is C10H10C18 (molecular weight = 414) and its reported
solubility in water ranges from 37 ,g/L (Lee et al. 1968) to over 500 ,g/L
(Paris et al. 1977). It is slowly dechlorinated photolitically (Callahan
et al. 1979) and by heat at about 120°C; breakdown is accelerated by
alkaline conditions and by iron catalysis.
Toxaphene was the most heavily used pesticide in the U.S. during the
1960s and 1970s, with annual applications totalling many millions of
kilograms (Pollock and Kilgore 1978; Ribick et al. 1982). It was frequently
mixed with DDT, methyl parathion, and other pesticides to improve its
effectiveness. It has been employed against insect pests of cotton, tobacco,
forests, turf, ornamental plants, grains, vegetables, and livestock, most
heavily in the southern U.S. and in California. Toxaphene was used as a
* An understanding of the "Guidelines for Deriving Numerical National Water
Quality Criteria for the Protection of Aquatic Organisms and Their Uses
(Stephan et al. 1985), hereafter referred to as the Guidelines, and the
response to public comment (U.S. EPA 1985a) is necessary in order to
understand the following text, tables, and calculations.
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replacement in many of Che former uses of DDT, after it was banned in 1971.
In 1976 toxaphene was close behind methyl parathion as the second most
heavily used insecticide in the "delta states" of Arkansas, Louisiana,
and Mississippi (0.2 million kilograms) and was the sixth most heavily used
insecticide in the corn belt (0.2 million kilograms) (Schmitt and Winger
1980). Use in California in the 1970s averaged 1.7 million kilograms per
year (Cohen et al. 1982). In addition, 0.7 million kilograms was applied
to a wide range of major agricultural crops in 12 north-central states in
1978 (Acie and Parke 1981) and 0.5 million kilograms in 1981 (Zygadlo 1982).
Toxaphene's relatively low toxicity to honey bees compared to that, of many
other insecticides favored its agricultural use (Eckert 1949). Only very
small quantities of toxaphene have been used agriculturally in Canada
(Department of National Health and Welfare 1977). It was also used in the
1950s and early 1960s by fisheries personnel in several U.S. states and
Canadian provinces to remove unwanted fish from lakes and ponds. This use
was discontinued or prohibited when an unexpectedly high persistence was
discovered in some lakes.
The U.S. EPA cancelled the registration of toxaphene for all uses in
November, 1982, except for treatment of cattle and sheep for scabies, of
pineapples for mealybug and gummosis moth, of bananas for weevils, and for
emergency treatment of cotton, corn, and small grains for armyworms, cutworms,
and grasshoppers. Some existing stocks of cancelled products could be sold
and used according to label specifications through December 31, 1986, and
all other stocks through 1983. Nor-Am Agricultural Products, Inc., the
principal North American manufacturer, discontinued production in 1982.
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The estimated use of toxaphene iu 1982 was 4.1 million kilogram, (personal
communication from Robert Hitch, U.S. EPA, Washington, DC to Larry Fink,
U S. EPA, Chicago, IL). The reported U.S. stocks totalled about 6 Billion
Ulograms in 1983 and Nor-Am reported it .till had about 3.6 million kilograms
until 1985 (personal communication, Jay Ellenberger, U.S. EPA, Washington,
DC). The Canadian registration for all pesticidal uses of toxaphene was
revoked in October, 1980, except for a minor use by veterinarians for
treatment of hogs for lice.
Capillary gas chromatography, sometimes in combination with mass
spectrometry, is the most frequently used analytical method for characterization
and quantitation of toxaphene in environmental samples (Ribick et al. 1982).
A typical toxaphene gas chromatogram contains many peaks, a few of which
are selected to distinguish toxaphene from other possible environmental co-
contaminants. The identification and quantification of toxaphene in water
' and fish tissues is 'complicated by changes in the numbers and relative
slzes of constituent peaks because of their differing rates of degradation,
sorption, and volatilization in the environment.
Changes in environmental sample chromatograms as compared.to reference
standard chromatograms have led some analysts to refer to their values as
"toxaphene-like" substances, although the prevailing uncertainty in
identification using the latest analysis techniques is small. Durkm et
al. (1979) reported a lower limit of detection of about 5 to 10 ng of toxaphene
by several GC detection methods, but more recent measurements down to 1 to
2 ng are not uncommon. Concentrations have been quantitatively measured
down to 0.1 ,g/g in fish tissues (Ribick et al. 1982) and down to 0.01 ,g/g
in extracted Hpid (Wideqvist et al. 1984).
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The compositional changes that occur in the field probably also mean
that field toxicity differs to some unknown extent from toxicity determined
in laboratory tests using technical-grade toxaphene. Using mice, houseflies,
and goldfish, Khalifa et al. (1974), Saleh et al. (1977), and Turner et al.
(1975,1977) demonstrated that different toxaphene components have substantially
different toxicities. Toxaphene that had "weathered" for 10 months in a
lake was altered chemically (diminution of late eluting peaks) and was
somewhat less toxic to fish than the original formulation (Lee et al. 1977).
In contrast, Harder et al. (1983) found that sediment-degraded products of
toxaphene were more toxic than the parent material to some saltwater fishes.
Applications of toxaphene to lakes for the purposes of fisheries
management have provided substantial amounts of data concerning its aquatic
fate and effects. Reports are available on the treatment of water bodies
in at least a dozen states and three Canadian provinces. Most of these
studies were conducted to determine the persistence of toxaphene in lakes
and to determine how soon lakes could be restocked after treatment to
eliminate unwanted species of fish. Treatment concentrations were usually
between 5 and 200 pg of toxaphene per liter of lake water, with higher
concentrations being recommended for warmer, shallower, and more turbid
lakes (Rose 1958). Persistence of toxicity to fish was highly variable,
ranging from a few weeks (e.g., Mayhew 1959) to greater than five years in
Miller Lake, Oregon (Terriere et al. 1966). Concentrations of toxaphene in
water typically dropped rapidly within a day or two after application due
to sorption to suspended particulates or sediment (Veith and Lee 1971).
Concentrations then diminished much more slowly for an indefinite period
(Kallman et al. 1962). Toxaphene persisted longest in hypolimnetic areas
of the most oligotrophic lakes (Stringer and McMynn 1960; Terriere et al.
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1966>. although it was detected at 1 to 4 M,/t for up to 10 year, after it
wa, applied to shallow eutrophlc lake, i. "i'consin (Johnson .e .1. 1966).
Various studies (e.g., Chandurkar and Matsumura 1979; Chandurkar et
ml 1,78; Hughe, et .1. 1970; Isen.ee et al. 1979; Saleh et .1. 1977, hav.
de.onstraced that toxaphene can be metabolised or degraded both aerobicaUy
and anaerobically. Quantitative data on degradation in water are lacUng
although it i, obviously very slow under ,ome conditions. Smith and WUHs
(1,78) observed a rapid disappearance of toxaphene from Mississippi soil
under anaerobic Uboratory conditions, but it «. not deter.i»ed whether
the disappearance .as due to binding to soil particle,, biological breakdown,
or other factors. Nash and Woolson (1967, estimated th. half-life of
to,aphene to be 11 years in soil. Toxaphene is not readily desorbed back
into water from contaminated sediments (Veith and Lee 1971,, aUhough it
can be cycled within aouatic ecosystems through the benthos-water column
food web connection, (Kallman et al. 1962; Rice and Evans 1984). Concentration,
approaching 2,000 mg/kg were found in an estuary adjacent to a toxaphene
pit discharge, and oyster, two miles away had concentrations a, high as 6
mg/kg (Durant and Reinold 1972).
In addition to sharply elevated concentrations in air in the immediate
vicinity of applications (e.g., Sieber et al. 1979; Stanley et al. 1971),
airborne transport of toxaphene over several hundred kilometers has also
been observed. Bidleman and Olney (1975) measured concentrations in the
air over the northeastern U.S., presumably carried from cotton growing
areas of the southern U.S., that were more than 10 times those of other
pesticides reported from the same areas. Ohlendorf et al. (1982) detected
toxaphene residues in the eggs of 15 of the 19 species of island-nesting
Alaskan sea birds they examined. Zell and Ballschmiter (1980) found residues
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in fish (0.068 to 3.5 mg/kg of extractable Lipid) coLLecCed from pristine
sites in the Tyrolian Alps, Northwest Ireland, Caspian Sea, and the North
Atlantic, North Pacific, and Antarctic Oceans. They suggested that such
wide distribution of toxaphene residues has created "an overall global
pollution larger than that by PCB."
Rice et al. (Manuscript) monitored atmospheric concentrations of
toxaphene in the summer and fall of 1981 at four locations between Greenville,
Mississippi, and northern Lake Michigan. Several lines of evidence indicated
the cotton belt as a source of toxaphene in Lake Michigan: a decrease
in number of matching GC chromatogram peaks from south to north; a reduction
in concentrations (7.39 ng/m^ in Greenville, 1.18 ng/m3 in St. Louis, 0.27
ng/m3 at Lake Michigan) from south to north; corresponding temporal
concentration patterns (all higher in summer); and a net south to north
wind flow pattern. The authors estimated a total toxaphene flux to Lake
Michigan of 3,360 to 6,720 kg in 1981. Agricultural use of toxaphene in
the north central states has been proposed as another possible source. No
information could be located on current use of toxaphene in Mexico, or
Central or South America; therefore the possibility of long-range transport
from there to the U.S. is unfathomable. However, facilities for the
production of toxaphene are known to have existed in these areas (personal
communication, Office of Pesticide Programs, U.S. EPA).
Because toxaphene is a mixture of many organic chemicals, "pure"
toxaphene has many components and is the same as "technical-grade toxaphene."
Thus the term "active ingredient" is interpreted to mean "technical-grade
toxaphene," that is, "toxaphene." The criteria presented herein supersede
previous aquatic life water quality criteria for toxaphene (U.S. EPA
1976,1980) because these new criteria were derived using improved procedures
6
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and add^onal -formation. Whenever adequately just^ed, a national
ctil.tiM .ay be replaced by a SLte-spec.fic cruer^on (».». «» "«•'•
uhich My include not only sUe-specUic criterton concentrates
(0 s EPA 19Mb), but also site-specU ic durations of averaging P«iod. and
slte-specHic frec.enoes o£ allo-e, «cutsions (U.S. SPA I9«b). »,. !atesc
™
recent L.f.n»tLo. .i*.t have ^ i«lud«l.
U July, 1986; so«e
^.^ TnvAcitv to Aquatic Animals
AcUte toxicity data tb.t a,e «..pt.bl. for driving »ater ,.aUty cri««U
are presented i» TabU 1. Fre^ace, data „. Ust.d in o,der of phylogeny,
then £OT iovest to hi5hest te.perat.re .UhL. a species, and tnen £ro«
,oungest to oldest Ufe stage at each test te.pe.atuce. for boU cnannel
catfish (taole 1) and the leopard frog (Table 6), ear!y exogeno.sly feed.ng
Ufe stages »ere »ore sensUive than i.iti.1 (^ dependent) or later life
Stages. Adults of ooch species appear to be the least sensU.ve Ufe stage.
in »« cases vhere the influence of temperature »as exa^ned (e.g., Cope
1,64; Hooper and Gr.enda 1955; Johnson and Julin 1980; Mace, et al. 1969;
Mahdi 1966; «ortaan and NeuhoU 1963), toxicity »as greater at higher te«per-
atures. The data obtained by Crosby et al. (1966) »ith Daphnia Haffia. constUute
a notable contradiction (Table 6), but the tests only lasted for 26 hr.
«here the effects of additional factors (e.g., .«« ,u.Llt, condU.ons,
source of test organls.s) on toxic.ty -ere Uvest .gated, these are .deat^ed
in the temperature colu»n of Table 1 and the effect co!u«n of TabU 6.
The »« »ell controHed e.perUents concerning the effects of «ater cuaUt,
»ere conducted with channet catfish by Johnson and Julin 11980) and
indicated little or no influence on toxicity. Henderson et al. (1959)
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obtained similar results with the fathead minnow. Data generated using water
from different sources (Sanders 1972; Workman and Neuhold 1963) indicate
greater differences in toxicity but the causal factors are unclear and the
effects might not be attributable to the measured water quality conditions.
Henderson et al. (1960) and Workman and Neuhold (1963) investigated
the influence of formulation on toxicity and found essentially no differences,
based on active ingredient, between technical-grade toxaphene and commercial
formulations with percentages of active ingredient ranging from 10 to 62.6%
(Table 1).
Toxaphene is relatively insoluble in water and tends to sorb onto
solid surfaces and particulates, especially those containing organic
materials. Actual concentrations of toxaphene in water are almost always
lower than amounts introduced into either flow-through or static test
systems, but are particularly lower in static tests. For example, Hall and
Swineford (1981) measured an average of only 30.57. of the intended water
concentrations in a secies of static acute tests, whereas in a series of
continuous-flow exposures they obtained 55.4% of the amounts intended in
their test solutions. Although other flow-through tests probably maintained
water concentrations somewhat closer to calculated values, most of the
unmeasured acute values are probably higher than the actual concentrations
of toxaphene in solution in exposure chambers.
Three stonefly species and eleven fish species have acute values
between 0.8 and 8 Mg/L (Table 3), whereas all of the tested freshwater species
with acute values between 20 and 500 ,jg/L are amphibians and invertebrates.
The few values that are available for freshwater algae are between 100 and
1,000 >Jg/L (Table 4). These laboratory data appear to correlate well with the
substantial body of information from field studies related to fish eradication.
8
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All fish spec.es were found to be similarly sensitive in the field, bat older
fi.h were .ore resistant than young ones (e.g., Henegar 1966). Treatment
concentrations recommended for fast, complete eradication of fish (10 to
200 ,g/L depending on water quality) correspond well with LC50s obtained
with fish in laboratory studies (e.g., Gushing and Olive 1956; Hemphill
1954; Henegar 1966; Kallman et al. 1962; Needham 1966; Rose 1958; Stringer
and McMynn 1958; Webb 1980; Woolitz 1962). Field results also agree with
one another and with the laboratory data that many invertebrate species are
less sensitive than fish; that some midges (especially Chaoborus sp.),
amphipods, copepods, cladocerans, protozoans, and odonates are among the
raost sensitive invertebrates (also Hilsenhoff 1965). Oligochaetes, snails,
leeches, and many insects are more resistant, whereas plants and phytoplankton
are quite resistant.
Species Mean Acute Values (Table 1) were calculated as geometric means
of the available acute values, and then Genus Mean Acute Values (Table 3)
were calculated as geometric means of the available freshwater Species
Mean Acute Values. Of the 28 freshwater genera for which acute values are
available, the most sensitive genus, Claassenia. is 385 times more sensitive
than the most resistant, Pseudacris. Acute values are available for more
than one species in each of eight genera, and the range o£ Species Mean
Acute Values within each genus is less than a factor of 4.4. The nine most
sensitive genera are all within a factor of 4 and include two stoneflies,
the common carp, and several important fish species including the
channel catfish, largemouth bass, coho and chinook salmon, rainbow and
brown trout, and striped bass. The freshwater Final Acute Value for
toxaphene was calculated to be 1.467 ,g/L using the procedure described in
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the Guidelines and Che Genus Mean Acute Values in Table 3. This is higher
than the Species Mean Acute Value for the important channel catfish, but
the value for this species was not based on the results of a flow-through
test in which the concentrations of toxaphene were measured.
Acute toxicity values for saltwater animals that are useful for deriving
water quality criteria are from tests with nine invertebrate and six fish
species. The sensitivities of the tested species range from 0.53 ,jg/L for
for juvenile pinfish, Lagodon rhombiodes (Schimmel et al. 1977) to 460,000
^g/L for adults of the clam, Rangia cuneata (Chaiyarach et al. 1975).
Acute values for stage II and III larvae of the drift line crab, Sesaraa
cinereum, were 0.5542 and 0.5298 >jg/L, respectively (Courtenay and Roberts
1973) which are similar to the acute value for the pinfish. Except for
resistant soecies tested at concentrations greater than toxaphene's solubility
in water, acute values for most species range from 0.53 to 31.32 >^g/L.
Fishes and invertebrates are similarly sensitive.
Limited data are available on the effect of water quality on the
toxicity of toxaphene. The toxicity of toxaphene to adult blue crabs,
Callinectes sagidug.. decreased slightly with increase in salioUy (Mahood
et al. 1970; McKenzie 1970). They report somewhat greater toxicity,to this
species at 10'C and 21°C than at 15'C at salinities of 8.6, 19.3, and 24.2
g/kg (Table 1). In contrast, the toxicity of toxaphene to adult threespine
stickleback, Gasterosteus aguleatog.. was similar at salinities oE 5 and 25
g/kg. The 96-hr LCSOs at these salinities were 8.6 and 7.8 ^g/L, respectively
(Katz 1961).
Harder et al. (1983) found that the acute toxicities of "parent" toxaphene
and "sediment-degraded" toxaphene were similar for the spot, Leiostoraus
10
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xanthurus, but that "sediment-degraded" toxaphene was about three times
raore toxic to the white mullet, Muj>il_ curema, (Tables 1 and 6).
Of the fifteen saltwater genera for which acute values are available, the
most sensitive, Lagodon, is over 867,000 ti.es .ore sensitive than the
most resistant, Rangia. but the two most resistant genera differ by a factor
of 411. The four most sensitive genera include three fishes and an
invertebrate, and the range of sensitivities is only a factor of 2.1.
The saltwater Final Acute Value was calculated to be 0.4197 ,g/L, which is
below the acute value for the most sensitive species.
rnvrnni^JToxicity to Aquatic Animals.
The freshwater chronic data indicate about one to two orders of magnitude
greater sensitivity than the acute data for the same species (Table 2).
Effects were observed at the lowest exposure concentration, 0.039 ,g/L, in
the brook trout partial life-cycle test conducted by Mayer et al. (1975).
The chronic value for the fathead minnow is 0.03674 Mg/L, whereas that for
the channel catfish is 0.1964 ,g/L. The one chronic value available for an
invertebrate is 0.09165 Jg/L for Daphnia magna.
The chronic toxicity tests that have been conducted with saltwater species
include an early life-stage test (Goodman et al. 1976) and a life-cycle test
(Goodman 1986) with the sheepshead minnow, C^^rinodon varie^atus, an early
life-stage test with the longnose killifish, Fjmdulus. similis (Schimmel et
al. 1977), and a life-cycle test with the mysid, MjrsidoHsis bahia (Kuhn and
Chammos 1986). Survival of sheepshead minnows was significantly reduced in
2.5 ,g/L and no effects on survival or growth were detectable in 1.1 «/L
in the 28-day early life-stage toxicity test. In a life-cycle test that
Lasted 192 days with the same species, 1.0 ,g/L reduced survival of both the
11
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first and second generations. Average length of fish after 28 days of
exposure to 1.0 ^g/L was reduced; however, for the remainder of the
exposure, growth was not impaired. Effects of toxaphene on survival,
growth, or reproduction of the sheepshead minnow were not detected in
0.51 rJg/L. Survival of longnose killifish was reduced in all concentrations
of toxaphene tested in the early life-stage test; fry survival was reduced
in 1.3 ,Jg/L. In the life-cycle test with the mysid, no adverse effects
on survival, growth, or reproduction were detected at a toxaphene concentration
of 1,585 ,Jg/L, which was the highest concentration tested. The 96-hr
LC50 of 2.03 jjg/L was used as the upper chronic limit.
Freshwater acute-chronic ratios are available for two fish species and
one invertebrate species. The acute sensitivities of these three species
only range from 5.5 to 10 ug/L, but the acute-chronic ratios range from 28
to 196. In the chronic test with a third fish species, the brook trout,
all tested concentrations of toxaphene caused unacceptable effects. The
only acute value available for this species was obtained in a test with
yearlings, not juveniles. The available data on freshwater acute-chronic
ratios do not allow calculation of a freshwater Final Chronic Value, but
if one could be calculated it would have to be less than the 0.039 gg/L
that adversely affected brook trout in a partial life-cycle test.
Two acute-chronic ratios are available for the saltwater sheepshead
minnow, but because the life-cycle test takes precedence over the early
life-stage test, the acute-chronic ratio for this species is 1.540. A
ratio of 1.133 was obtained with a mysid. Both of these ratios are much
smaller than the two ratios that were obtained with freshwater species.
However, according to the Guidelines, the saltwater Final Acute-Chronic
Ratio cannot be less than 2. Thus the saltwater Final Chronic Value for
12
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toxaphene is equal Co the Criterion Maximum Concentration of 0.2098 ,g/L
(Table 3).
Toxicity to Aquatic Plants
Two freshwater green algae were affected by toxaphene concentrations
fro, 100 to 1,000 ,g/L (Table 4). These species are less sensitive than
most annals and indicate that freshwater plants are likely to be protected
by criteria that protect freshwater animals. These conclusions are also
supported by results of studies concerning use of toxaphene to eradicate
fish.
Toxicity tests have been conducted in salt water with five species of
phytoplankton and with natural phytoplankton communities (Table 6). Four
of the five species were affected in ten days at toxaphene concentrations
ranging from 10 to 70 ,g/L (Ukeles 1962). The fifth species, Monochrysis
lutheri_, was particularly sensitive with 0.15 ,g/L preventing growth and
0.015 Mg/L causing a 22% reduction in growth.
Bioaccumulation
Toxaphene has been found frequently in tissues of birds and aquatic
organisms both near to and far from primary use sites, e.g., eggs of island-
nesting sea birds in Alaska (Ohlendorf et al. 1982); eggs of waterbirds and
waterfowl from Lake Michigan (Haseltine et al. 1981: Heinz et al. 1985);
shore birds and gulls in Texas (White et al. 1980,1983); terns in southern
California (Ohlendorf et al. 1985); fish-eating birds (Ohlendorf et al.
1981) and eagles (Wiemeyer et al. 1984) across the U.S.; ducks in California
(Ohlendorf and Miller 1984), Arizona and New Mexico (Fleming and Cain 1985),
Maryland (White et al. 1979) and Maine (Szaro et al. 1979); brown pelicans
in Texas (King et al. 1985) and Louisiana (Blus et al. 1975); Canadian east-
13
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coast saltwater fish (MusiaL and Uthe 1983); birds and several kinds of
aquatic organisms from the Apalachicola River in Florida (Elder and Mactraw
1984; Winger et al. 1984) and Louisiana oxbow lakes (Niethammer et al.
1984); and various fish species in Alabama (Grzenda et al. 1964), Texas
(Dick 1982), the Colorado River (Johnson and Lew 1970), California (Keith
and Hunt 1966), South Dakota (Hannon et al. 1970), and the Mississippi
River delta (Crockett et al. 1975; Epps et al. 1967; Hawthorne et al.
1974). Some mortalities of birds have been associated with agricultural
applications of toxaphene (e.g., Ginn and Fisher 1974; Keith 1966), although
some of these have involved contamination by other pesticides as well
(Keith 1966; Plumb and Richburg 1977).
In a summary of data on the concentrations of toxaphene in Great Lakes
fish through 1981, Rice and Evans (1984) reported that residues'increased
through the 1970s and that fish in. Lake Michigan contained higher concentrations
than those from the other lakes. Like other chlorinated hydrocarbon
pesticides, toxaphene is lipophilic and the highest concentrations are
usually in the oldest and fattest fish at the top of the food chain, such
as lake trout. Concentrations in this species have generally ranged between
1 and 10 mg/kg in the most recently published analyses (Canada Department
of Fisheries and Oceans 1982; Rice and Evans 1984; Schmitt et al. 1985).
Schmitt et al. (1985) reported that toxaphene residues seemed to have peaked
nationally in U.S. freshwater fish collected in 1980 and 1981, even though
it was more widely distributed than in previous surveys. Residues in Great
Lakes fish, especially those from Lakes Michigan and Superior, generally
appeared 2 to 5 mg/kg lower than the 5 to 10 mg/kg commonly observed during
the 1970s. Adult lake trout collected from Lake Huron near Rockport,
Michigan in 1984 contained 2.2 mg/kg; bloater chubs collected from Lake
14
-------
Michigan near Saugatuck, Michigan in 1982 contained 1.6 mg/kg, whereas
those collected in the same area in the fall of 1984 contained 2.2 mg/kg
(personal communication, Robert Hesselberg, U.S. Fish and Wildlife Service,
Great Lakes Fishery Laboratory, Ann Arbor, Michigan). All reported values
are for concentrations in whole fish, which are probably somewhat higher
than concentrations in edible tissue. Clark et .1. (1984) reported
"apparent toxaphene" residues in coho salmon fillets at below 0.5 mg/kg in
La.es Erie and Superior, and up to nearly 2 mg/kg in Lake Michigan and Lake
Huron. "Toxaphene-like" residues have been measured in fillets of lake
trout from the mouth of Saginaw Bay in Lake Huron at up to 26 mg/kg
(Swain et al. 1986).
The concentration of toxaphene in samples of water collected in 1980
from 5 stations in Lake Huron ranged from 1.2 to 2.1 ng/L and averaged 1.6
ng/L (Swain et al. 1986). Although these are referred to as "toxaphene-
Uke" materials, the analysts feel quite certain that the observed residues
were derived from chlorinated camphene (personal communication, Mike Mullin).
Swain et al. (1986) also reported "toxaphene-like" residues in Siskiwit
Lake on Isle Royale in Lake Superior at 2.2 ng/L. Five composites of lake
trout from Siskiwit Lake averaged 4.2 mg/kg and a cross-check of these
analyses by the U.S. Fish and Wildlife Service laboratory in Columbia,
Missouri measured 3.2 mg/kg. Toxaphene has been measured in the water at
several additional sites around Lake Superior since 1982 (personal
communication, Steve Eisenrich, University of Minnesota, Minneapolis).
Concentrations in water ranged from 1 to 4 ng/L with the higher values
being present at the western end of the lake. Measurements of the
concentration of toxaphene in water are not known to'exist for the other
Great Lakes.
15
-------
Bioconcentration data from laboratory tests with fish indicate that
steady-state between concentrations of toxaphene in water and tissue is
reached by about 30 days of exposure. Pooling of all fish whole body data
in Table 5 provides a geometric mean bioconcentration factor (BCF) of
15,000. Daphnia magna accumulated 4,000 times the water concentration of
toxaphene. These values are similar to the bioaccumulation factors (BAFs)
observed by Terriere et al. (1966) in several stocked fish species and
other aquatic organisms from two Oregon lakes studied over a 3-year period
during recovery after a fish eradication treatment. Invertebrate residues
ranged between 1,200 and 2,500 times water concentrations, and aquatic
plants had BAFs of 500 to 7,000. BAFs for fish ranged from 9,000 to 19,000
for rainbow trout, 4,000 to 8,000 for Atlantic salmon, and averaged 15,000
for brook trout. Residues in caged rainbow trout introduced into one of
the lakes indicated that steady-state might have been reached between 38
and 46 days of exposure. The similarity of the laboratory BCFs (direct
uptake) and field BAFs — within a factor of 3 or 4 for fish and
invertebrates — indicates little or no additional contribution from the
food chain.
In contrast, factors of 1,250,000 to 25,000,000 would be required to
produce residues of 5 to 25 mg/kg in lake trout in the Great Lakes (Rice and
Evans 1984; Swain et al. 1986) from toxaphene concentrations of 1 to 4
ng/L in water. Because toxaphene is not known to be used or discharged in
substantial quantities near the Great Lakes, and especially near Siskiwit
Lake on Isle Royale, it is likely that the toxaphene entered the water from
the air and that the high concentrations in fish are not due to localized
"hot spots." Possible reasons for the differences between the various data
include: a higher percent lipid in lake trout than in other, usually less
16
-------
fatty, fish species; inaccurate measurements of toxaphene; the existence of
food-web magnification of residues in Great Lakes fish not evident from
other studies (e.g., Oregon lakes); a much longer exposure period in Great
Lakes fish: localized concentrations of toxaphene in the Great Lakes that
are higher than those that have been measured to date; and differences in
the precise composition of the toxaphene being measured. Niimi (1985)
discussed the importance of food related bioaccumulation of highly persistent
organic chemicals, including toxaphene, and concluded that much higher
tissue residues would be expected in adult salmonids in the Great Lakes
than in fishes exposed in laboratory tests.
For saltwater organisms, uptake data from tests lasting 28 days or
longer are available for the eastern oyster, Crassostrea vir^inica. and two
saltwater fishes, Cyprinodon variegatus and Fundulus similis. (T*ble 5).
The bioconcentration factor (BCF) for edible tissue from oysters exposed to
0.7 and 0.8 ;Jg/L for from 84 to 252 days averaged 13,350 (Lowe et al. 1971).
After 12 weeks of depuration, no toxaphene could be detected in oyster
tissues. BCFs for toxaphene in sheepshead minnows are from an early life-
stage and a life-cycle test. A mean BCF of 9,380 was obtained with juvenile
fish that survived the early life-stage test (Goodman et al. 1976), In
the life-cycle test BCFs averaged 26,550 for first generation and 21,950
for second generation juveniles (Goodman 1986). BCFs in adult females
averaged 64,750 and in males 70,140. With longnose killifish, Fundulus
similis> BCFs averaged 22,640, 31,550 and 34,440 in 28-day exposures of
embryos and fry, fry, and juveniles, respectively.
The BCFs normalized to 1% lipids range from 1,463 to 28,700 (Table 5)
and the geometric mean is 6,195. By using the 10 and 11% lipids recommended
in the Guidelines for fresh and salt water, respectively, and the FDA action
17
-------
level of 5 tng/kg, the Final Residue Values for toxaphene are 0.07337 ,jg/L
for fresh water and 0.08071 ,jg/L for salt water. However, these Final
Residue Values based on laboratory-derived BCFs will not protect species
that accumulate toxaphene like the lake trout does. It is not unusual for
lake trout in the Great Lakes to exceed the FDA action level in the whole
body, even though the concentration of toxaphene in the water is apparently
only 1 to 4 ng/L. Because the percent lipids is so high in the edible
portion of lake trout, it is likely that the concentration of toxaphene in
the edible portion exceeds the FDA action level whenever the concentration
in the whole body exceeds it. Thus the concentration of toxaphene in water
apparently should not exceed 1 to 4 ng/L wherever lake trout is a consumed
species. Although some of the lake trout that exceeded the FDA action level
contained up to 31% lipids, others contained only 10 to 15% lipids (Rice and
Evans 1984; Swain et al. 1968), which is in the range of the mean percent
lipids reported for freshwater chinook salmon and lake trout, and saltwater
Atlantic herring (Sidwell 1981). Therefore, because an average concentration
of toxaphene in the Great Lakes of about 2 ng/L causes some lake trout to
exceed the FDA action level, there is cause for concern wherever the concen-
tration of toxaphene exceeds 0.0002 Mg/L in either fresh or salt water.
Other Data
Other data on the effects of toxaphene are presented in Table 6.
Sanders (1980) found that 0.18 ug/L reduced the growth of Gammarus. fasciatus_.
The behavior of goldfish was affected by 0.44 ^g/L (Warner et al. 1966), and
0.144 ,Jg/L inhibited cytochrome P-450 activity in bluegills (Auwarter 1977).
A biological factor influencing sensitivity to t.oxaphene is the
development of a resistance resulting from exposures killing the more
sensitive individuals in field populations. This phenomenon has been
18
-------
demonstrated for several fi.h and invertebrate spec.es (Table 6) collected
Ln areas of high agricultural use (Albaugh 1972; Bur.e and Ferguson 1969;
Dziu* and Plapp 1973; Ferguson 1968: Ferguson and Bingham 1966; Ferguson et
al. 1965a,b; Klassen et al. 1965; Naqvi and Ferguson 1968,1970). Levels of
resistance more than two orders of magnitude greater than for individuals
from areas uncontaminated with toxaphene have been detected in Mississippi
Delta mosquitofish (Ferguson 1968). The degree of resistance appears to
correspond to the level of contamination and to be genetically rather than
physiologically mediated. Yarbrough and Chambers (1979) concluded that
extreme resistance in mosquitofish was due primarily to target site
insensitivity, due to a lesser extent to elevated barriers to pesticide
penetration, and due very little to increased metabolism of toxaphene.
Schoettger and Olive (1961) found that Da£hnia magna exposed to multiple
sublethal concentrations of toxaphene could accumulate enough pesticide to
be lethal when fed to shiner minnows.
The number and abundance of saltwater arthropods that colonized sand-
filled aquaria receiving 11 .g of toxaphene/L for three months were significantly
reduced and the abundances of annelids and molluscs were increased (Hansen
and Tagatz 1980). No effects on benthic colonization were observed at 0.77
^g/L. The 96-hr EC50s from three oyster-shell deposition tests ranged from
16 to 38 ng/L (Butler 1963; Lowe et al. 1970; Schimmel et al. 1977; U.S.
Bureau of Commercial Fisheries 1965). No effects on growth or histopathology
were observed in oysters exposed for 9 months to 0.7 ^g/L (Lowe et al.
1971). Three species of shrimp were more sensitive to toxaphene. The
48-hr EC50s, based on death plus loss of equilibrium, ranged from 2.7 to
5.2 ^g/L (Butler 1963: Lowe et al. 1970; U.S. Bureau'of Commercial Fisheries
1965). Historical alterations were observed in 96-hr exposures of blue
19
-------
crab stage II larvae to 0.0072 >Jg/L, mud crab Larvae to 7.16 ,jg/L, and drift
line crab larvae to 0.0215 Mg/L- Reproduction of the mysid, Mysidopsis
bahia, was reduced 84% following exposure to 0.14 ^g/L for 14 days (Nimmo
1977; Nimmo et al. 1981). BCFs after 96-hr exposure averaged 11,000 for
eastern oysters, 526.4 for pink shrimp, and 948.6 for grass shrimp
(Schimmel et al. 1977).
Concentrations of toxaphene lethal to saltwater fishes decreased as the
duration of exposure increased. The 28-day LCSOs ranged from 0.9 to 1.4
jjg/L for early life stages of the longnose killifish, Fundulus similis
(Schimmel et al. 1977). The 48-hr LC50 for this species is 28 >jg/L (Lowe et
al. 1970). The 48- or 96-hr LC50s range from 1.0 to 3.2 ,Jg/L for the
juvenile spot, Leiostomus xanthurus (Butler 1964; Harder et al. 1983; U.S.
Bureau of Commercial Fisheries 1965). Exposure of this fish foT six days
to 0.5 iJg/L resulted in 50% mortality; exposure to 0.1 >Jg/L for five months
did not affect growth or survival (Lowe 1964). BCFs after 96-hr exposure
averaged 4,284 for sheepshead minnows, 3,850 for pinfish, 2,508 to 3,786
for spot, and 4,807 to 5,020 for white mullet (Harder et al. 1983; Schimmel
et al. 1977). BCFs for spot and mullet are from tests with parent and
sediment-degraded toxaphene and appear similar.
Blus et al. (1979a,b) reported an apparent linkage between the thickness
of shells of eggs of brown pelicans and organochlorine residues in the birds.
Unused Data
Data were not used if the tests were conducted with a species that is
not resident in North America. Results (e.g., Nelson and Matsumura 1975a,b)
of tests conducted with brine shrimp, Artemia sp., were not used because
these species are from a unique saltwater environment. Grahl (1983), Holden
20
-------
(1981), LeBlanc (1984), Mayer and Mehrle (1978), PollocR and Kilgore (1978),
von RumRer (1974), and Whitacre et al. (1972) only contain data that have
been published elsewhere.
Schaper and Crowder (1976) used fish from a sewage oxidation pond.
Data were not used if the organisms were exposed to toxaphene in food
(Haseltine et al. 1980; Loeb and Kelly 1963; Mehrle et al. 1979). Davis et al.
(1972), Desaiah and Koch (1977), Hiltibran (1974,1982), Moffett and Yarbrough
(1972), and Shea and Berry (1982a,b) only exposed homogenized tissues or
cell cultures. Gallagher et al. (1979) studied -the fate but not the
effects of toxaphene in saline marsh soils.
Results were not used if the test procedures were not adequately
described (e.g. , Applegate et al. 1957; Boyd 1964; Carter and Graves 1972;
Cohen et al. I960; Davidow and Sabatino 1954; Doudoroff et al. 1953; Lawrence
1950; Mills 1977; Nelson and Matsumura 1975b; Surber 1948) or if toxaphene
was a component of a mixture, effluent, or sediment (e.g., Durant and
Reimold 1972; Hall et al. 1984; Macek 1975; Rawlings and Samfield 1979;
Reimold 1974; Walsh et al. 1982; Weber and Rosenberg 1980). Khattat and
Farley (1976) obtained an atypical concentration-effect curve with Acjj^U
tonsa, and Lowe (1964) exposed too few organisms. Some values reported by
Courtenay and Roberts (1973) were not used because the test procedures were
not adequately described. No value was used for stage I larvae of the
drift line crab because two different values were reported and it is not
possible to decide which is correct.
Data on the concentrations of toxaphene in wild aquatic organisms were
not used to calculate bioaccumulation factors if the concentration of
toxaphene in the water was not measured often enough or if the concentration
varied too much (e.g., Ballschmiter et al. 1981; Blus et al. 1979a,b; Buhler
21
-------
et al. 1975; Butler 1973; Durant and Reimold 1972; Eisenberg and Topping
1984; Gallagher et al. 1979; Reiser et al. 1973; Klaas and Belisle 1977;
Munson 1976; Husial and Uthe 1983; Ohleadorf et al. 1981,1982; Refold aad
Durant 1974; Szaro et al. 1979; White et al. 1979,1980; Zell and Ballschmiter
1980). Zaroogiaa et al. (1985) predicted a BCF for toxaphene based on
structure-activity relationships.
Summary
The acute sensitivities of 36 freshwater species in 28 genera ranged
from 0.8 ;Jg/L to 500 ,g/L. Such important fish species as the channel
catfish, largemouth bass, chinook and coho salmon, brook, brown and rainbow
trout, striped bass, and bluegill had acute sensitivities ranging from 0.8
>jg/L to 10.8 Jg/L. Chronic values for four freshwater species range from
less than 0.039 «/L for the brook trout to 0.1964 ng/L for the channel
catfish. The growth of algae was affected at 100 to 1,000 ,jg/L, and
bioconcentration factors from laboratory tests ranged from 3,100 to 90.UOO.
Concentrations in lake trout in the Great Lakes have frequently exceeded
the U.S. FDA action level of 5 mg/kg, even though the concentrations in the
water seem to be only 1 to 4 ng/L. These concentrations in the lake water
are thought to have resulted from toxaphene being transported to the Great
Lakes from remote sites, the locations of which are not well known.
The acute toxicity of toxaphene to 15 species of saltwater animals
ranges from 0.53 for pinfish, Lagodon rh^oides., 'o 460>000 «/L f°C the
adults of the clam, Ran^ia c_uneata. Except for resistant species tested at
concentrations greater than toxaphene's water solubility, acute values for
most species were within a factor of 10. The toxicity of toxaphene was
found to decrease slightly with increasing salinity for adult blue
22
-------
crabs, CalUnectessapidus. whereas no relationship between toxicity and
salinity was observed with the threespine stickleback, Gasteroste- .cule-tu..
Temperature significantly affected the toxicity of toxaphene to blue crabs.
Early life-stage toxicity tests have been conducted with the sheepshead
.innow, Cv.Hrinodon vari-gsta., and the longnose killifi.h, Fundulus. simiUs,
whereas life-cycle tests have been conducted with the sheepshead minnow and
a mysid. For the sheepshead minnow, chronic values of 1.658 ,g/L from the
early life-stage and 0.7141 ,g/L from the life-cycle toxicity test are
similar to the 96-hr LC50 of 1.1 «/L. Killifi-h are more chronically
sensitive with effects noted at 0.3 ,g/L. In the life-cycle test with the
mysid, no adverse effects were observed at the highest concentration tested,
which was only slightly below the 96-hr LC50, resulting in an acute-chronic
ratio of 1.132.
Toxaphene is bioconcentrated by an oyster, Crasj^tj^a virglnica, and
two fishes, C. variegatus and F. amili., to concentrations that range from
9,380 to 70,140 times that in the test solution.
National Criteria
The procedures described in the "Guidelines for Deriving Numerical
National Water Quality Criteria for the Protection of Aquatic Organisms and
Their Uses" indicate that, except possibly where a locally important species
is very sensitive, freshwater aquatic organisms and their uses should not
be affected unacceptably if the four-day average concentration of toxaphene
does not exceed 0.0002 «/L more than once every three years on the average
and if the one-hour average concentration does not exceed 0.73 Mg/L more
than once every three years on the average. If the concentration of toxaphene
does exceed 0.0002 ^g/L, the edible portions of consumed species should be
23
-------
analyzed to determine whether the concentration of toxaphene exceeds the
FDA action level of 5 mg/kg. If the channel catfish is as acutely sensitive
as some data indicate it might be, it will not be protected by this criterion.
The procedures described in the "Guidelines for Deriving Numerical
National Water Quality Criteria for the Protection of Aquatic Organisms and
Their Uses" indicate that, except possibly where a locally important species
is very sensitive, saltwater aquatic organisms and their uses should not be
affected unacceptably if the one-hour average concentration of toxaphene
does not exceed 0.21 pg/L more than once every three years on the average and
if the four-day average concentration of toxaphene does not exceed 0.0002
pg/L more than once every three years on the average. If the concentration
of toxaphene does exceed 0.0002 yg/L, the edible portions of consumed
species should be analyzed to determine whether the concentration of
toxaphene exceeds the FDA action level of 5 mg/kg.
Three years is the Agency's best "scientific judgment of the average
amount of time aquatic ecosystems should be provided between excursions
(U.S. EPA 1985b). The resiliencies of ecosystems and their abilities to
recover differ greatly, however, and site-specific allowed excursion
frequencies may be established if adequate justification is provided.
Use of criteria for developing water quality-based permit limits and
for designing waste treatment facilities requires selection of an appropriate
wasteload allocation model. Dynamic models are preferred for the application
of these criteria (U.S. EPA 1985b). Limited data or other considerations
might make their use impractical, in which case one must rely on a
steady-state model (U.S. EPA 1986).
24
-------
Table I.
Acute Toxiclty of Toxaphene to Aquatic A»l»als
N3
Species
Cladoceran (1st Instar),
Daphnla magna
Cladoceran (1st Instar),
Daphnla magna
Cladoceran (^24 hr),
Daphnla magna
Cladoceran (1st Instar),
Daphnla pulex
Cladoceran (1st Instar),
Daphnla pulex
Cladoceran (1st Instar),
Slmocephalus serrulatus
Cladoceran (1st Instar),
Slmocephalus serrulatus
Am phi pod,
Gammarus fasclatus
Am phi pod,
Gammarus fasclatus
Am phi pod,
Gammarus fasclatus
Amphi pod (2 mo. old),
Gammarus lacustrls
Amphlpod (early Instar),
Gammarus pseudolImneaus
Prawn (late Instar),
Palaemonetes kadlakensls
Prawn (25-31 mm),
Palaemonetes kadlakensls
Method*
S,M
S.U
S.U
S,U
S.U
S.U
s.u
s.u
s,u
s.u
s.u
S,M
s.u
FRESHWATER SPECIES
18
21
23
15
4
15.6
21.1
21
(son water)
21
(hard water)
21
21.1
21
10
10
155*
14.2
15
19
10
35
6
26
26
24
28
36
Species
Acute Value
(>g/L)
10
14.
13.78
17.61
26
24
Sanders 1980
Johnson and Flnley 1980
Bring man n and Kuhn 1960
Johnson and Flnley 1980
Sanders and Cope 1966
Sanders and Cope 1966;
Johnson and Flnley 1980
Sanders and Cope 1966
Sanders 1972
Sanders 1972
Johnson and Flnley 1980
Sanders 1969
Sanders 1980
Sanders 1972
31.75 Chalyarach et al. 1975
-------
IflDI* 1* \VAjni IHU»U/
Soectes
Crayfish (60-70 mm).
Procambarus slmulans
Stonefly (15-20 mm) ,
P teronar ce 1 1 a bad 1 a
Stonefly (30-55 mm),
Pteronarcys callfornlca
Stonefly (20-25 mm) ,
Claassenia sabulosa
Crane fly ( larva).
Tlpula sp.
Mldqe (4th Instar larva).
Chlronoreus plumosus
Midge (4th Instar larva).
Chlronomus plumosus
Snipe fly ( larva) ,
Atherlx varlegata
Coho salmon (1 g) ,
Oncorhvnchus klsutch
Coho salmon (0.6-1.7 g) ,
Oncorhynchus klsutch
Coho salmon (57-76 mm; 2.7-4.1 g) ,
Oncorhynchus klsutch
Chinook salmon.
Oncorhvnchus tshawytscha
Chinook salmon (51-114 mm;
1.45-5 g),
Oncorhynchus tshawytscha
Ra Inbow trout ( 1 g) ,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Method*
-.u
s,u
s.u
s.u
s.u
s.u
S.M
s.u
s.u
s.u
s.u
s.u
s.u
s,u
s.u
Test T
Material**
-
T
t
T
T
T
T
T
T
T
T
T
T
-
CS
emperature
CO
-
15.5
15.5
15.5
15
15
22
15
12
13
20
14.4
20
t
7.2
11.7
LC50 or
EC50 <»a/L)***
210
3.0
2.3
1.3
18
30
180
40
8
4.0
9.4
1.54
2.5
5.4
8.4
Species Mean
Acute Valae
(»q/L) Reference
210 Chalyarach et al . 1975
3.0 Sanders and Cope 1968
2.3 Sanders and Cope 1968;
Johnson and Flnley 1980
1.3 Sanders and Cope 1968;
Johnson and Flnley 1980
18 Johnson and Flnley 1980
Johnson and Finlay 1980
73.48 Sanders 1980
40 Johnson and Flnley 1980
Johnson and Flnley 1980
Macek and McAllister 1970
6.700 Katz 1961
Earnest 1970
1.962 Katz 1961
Copa 1964
Mahdi 1966
-------
10
TabU 1. (continued)
SP*cl*^
Rainbow trout (1.4 g) , s»u
Salmo qalrdnerl
Ra Inbow trout ( 1 g) , s»u
Salmo qalrdnerl
Rainbow trout (21 g), s«u
Salmo qalrdnerl
Rainbow trout (21 g) , s» u
Salmo qalrdnerl
Rainbow trout (0.6-1.7 g) , S,U
Salmo qalrdnerl
Rainbow trout ( 1 g) , s«u
Salmo qalrdnerl
Rainbow trout (Donaldson trout) S.U
(51-79 mm; 3.2 g) ,
Salmo qalrdnerl
Brown trout (1.7 g) , s»u
Salmo trutta
Brook trout (yearling; 133 g; F.M
231 mm).
Salve! Inus fontlnalls
Central stoneroller, s»u
r.ampostoma anoma 1 urn
Central stoneroller, s»u
r.ampostoma anoma 1 urn
Central stoneroller, s»u
Campostoma anoma 1 urn
C 1 1
Central stoneroller, 3»u
C ampostoma anoma 1 urn
Goldfish (4.2 g), s-u
T»st
•
Floating
(10*)
Sinking
(62.6*)
T
T
T
1
cs
cs
cs
Floating
(10*)
TMp«ratiir* LC50 or
(•C) EC50 *
12 '0.6
12.8 2.7
* f*. r\ OQ T T
12.8 28
12.8 23ft
11
13 1'
18.3 1.8
20 8«4
T 1
12 3«'
10 1°'8
11.7 H
11.7 7
17.2 32
22.7 ' <5
8.3 (pH 8.3, 26
IDS 166)
Sp*cUs NMM
Acute Vain*
(pO/L) R«t«r«»c«
Johnsan and Flnley 1980
Cope 1964
Workman and Neuhold 1963
5>782 Workman and Neuhold 1963
Macek and McAllister 1970
Cope 1964
Katz 1961
3 i Johnson and Flnley 1980
•*• 1
j
10.8 Mayer et al . 1975
Mahd 1 1966
w |*1dlKJ 1 1 7UV/
Mahdi 1966
u^hrl 1 1966
^ no i i*j • i ^v*^
-------
Table 1. (continued)
Species
Goldfish (4.2 g),
Carasslus auratus
Goldfish,
Carasslus auratus
Goldfish,
Carasslus auratus
Goldfish (1 g),
Carasslus auratus
Goldfish (4.2 g),
Carasslus auratus
Goldfish (4.2 g),
Carasslus auratus
Goldfish (4.2 g),
Carasslus auratus
Goldfish (4.2 g),
Carasslus auratus
Goldfish (4.2 g),
Carasslus auratus
Goldfish (4.2 g),
Carasslus auratus
Goldfish,
Carasslus auratus
Goldfish (6 on) ,
Carasslus auratus
Goldfish (1-2 g),
Carassius auratus
Common carp (0.6 g) ,
Method*
s,u
s.u
s.u
s.u
s,u
s,u
s.u
s.u
s.u
s.u
s.u
F.U
s.u
s.u
Test
Material**
Sinking
(62.6*)
CS
CS
T
Floating
(10*)
Sinking
(62.6*)
Floating
(10*)
Sinking
(62.6*)
Floating
(10*)
Sinking
(62.6*)
CS
T
Temperature
CO
8.3 (pH 8.3,
TDS 166)
11.7
17.2
18
20 (pH 8.3,
TOS 166)
20 (pH 8.3,
TDS 166)
20 (pH 7.8,
TOS 238)
20 (pH 7.8,
TOS 238)
20 (pH 7.0,
TOS 46)
20 (pH 7.0,
TDS 46)
' 22.7
25
25
18
Species Mean
LC50 or Acute Value
EC50 Ug/U*** (»a/L)
44
94
28
14
4
9
28
16
7
9
50
11
5.6 16.71
3.7 3.7
Reference
Workman and Neuhold 1963
Mahdl 1966
Mahdl 1966
Johnson and Flnley 1980
Workman and Neuhold 1963
Workman and Neuhold 1963
Workman and Neuhold 1963
Workman and Neuhold 1963
Workman and Neuhold 1963
Workman and Neuhold 1963
Mahdl 1966
Warner et al . 1966
Henderson et al . 1959
Johnson and Flnley 1980
Cyprlnus carplo
-------
Table 1. (continued)
Species
Golden shiner.
Notemlgonus crvsoleucas
Golden shiner,
Notemlgonus crvsoleucas
Bluntnose minnow.
Plmephales notatus
Bluntnose minnow.
Plmephales notatus
Bluntnose minnow,
Plmephales notatus
Fathead minnow (0.6-1.7 g) ,
Plmephales promelas
Fathead minnow (0.5-1.5 g) ,
Plmephales promelas
Fathead minnow (1.1 g) .
Plmephales promelas
Fathead minnow (0.5-1.5 g) ,
P Imephales promelas
Fathead minnow (0.5-1.5 g) ,
Plmephales promelas
Fathead minnow (30 day; 0.32 g;
30 mm), .
Plmephales promelas
Fathead minnow (0.5-1.5 g) ,
Plmephales promelas
Fathead minnow (1-2 g) ,
Plmephales promelas
Fathead minnow (1-2 g) ,
Plmephales promelas
Specie* Mean
Test Temperature LC50 or Acute Value
^*w~4« M^rl.|M CO EC50 Ua/L)*"" WL>
c ,, CS '7.2 <5
b.U <">3
OO T ft ^5 • 4 1 1
Sll P<* i£.ml ° -»•-•»»
,U V.5 "••
S.U CS 11-7 30
Ui A A ~
•2 '
a. i 11 ft^
S.U CS 22.7 6.3 •»•<"
S.U T 18 14 -
,. .. T 20 20
S.U T w
nf\ \ A ™
S.U T 20 18
F.U T 20 T '
__ C —
F.U T 25 5
.- . T •>*> 7.2
F.U T "
T 25 23
S.U T *•?
c a - 25 5''
C II ^ •• ^ **
' (hard water)'
su - 25 7'5 10'12
' (soft water)
Reference
Mahdl 1966
Mahdl 1966
Mahdl 1966
Mahdl 1966
. . . j | | Qf.fL
Mahd 1 19oo
Macek and McAllister 1970
Johnson and Jul In
Johnson and Flnley
Johnson and Jul In
Johnson and Jul In
Mayer et al . 1977
Johnson and Jul In
Henderson et al .
Henderson et al .
1980
1980
1980
1980
1980
1959
1959
-------
IBDIV 1. »fc»ll inuwu/
Species Method*
Black bullhead, S,U
Ictalurus melas
Black bullhead, S,U
Ictalurus melas
Black bullhead (0.6-1.7 g) , S.U
1 ctalurus melas
Black bullhead, S.U
Ictalurus melas
Black bullhead (0.9 g) , S.U
1 ctalurus melas
Channel catf ish ( flngerllng; S.U
0.5-1.5 g).
Ictalurus punctatus
Channel catfish (1.5 g), S,U
1 eta 1 ur us punctatus^
Channel catf Ish ( finger 1 Ing; S,U
0.5-1.5 g).
Ictalurus punctatus
Channel catf ish ( finger 1 Ing; S.U
0.5-1.5 g).
Ictalurus punctatus
Channel catfish (flngerllng; S.U
0.5-1.5 g).
Ictalurus punctatus
Channel catf Ish ( flngerl Ing; S,U
0.5-1.5 g).
Ictalurus punctatus
Test Temperature LC50 or
Material** <*C) EC50 d,g/L)"*"
CS 11.7 25tf
CS 17.2 2.7
T 18 5
CS 22.7 1.8
T 24 5.8
T 15 (pH 7.4, 4.7tf
alk 35, hard 40)
T 18 13.1tf
T 20 (pH 7.4, 4.2tf
alk 35, hard 40)
T 20 (pH 6.5, 2.7ft
alk 35, hard 10)
T 20 (pH 7.5, 3.4tf
alk 35, hard 40)
T 20 (pH 8.3, 3.0 tf
alk 35, hard 40)
Species Mean
Acute Value
( »g/L ) Reference
Mahdl 1966
Mahdl 1966
Macek and McAllister 1970
Mahdl 1966
3.446 Johnson and Finley 1980
Johnson and Jul in 1980
Johnson and Finley 1980
Johnson and Jul In 1980
Johnson and Jul In 1980
Johnson and Jul In 1980
Johnson and Jul In 1980
Channel catfish (0.5-1.5 g),
I eta Iurus punctatus
S.U
20 (pH 8.2,
oik 22G, hard 10}
3.9
tt
Johnson and Jul In 1980
-------
laDie 1. ICOHTinUBU/
Sp«cl«« Method*
Channel catfish (0.5-1.5 g) , S,U
Ictalurus punctatus
Channel catfish (0.5-1.5 g) , S,U
Ictalurus punctatus
Channel catfish (0.5-1.5 g) , S,U
1 eta 1 ur us punctatus
Channel catfish (4 g) , F,U
Ictalurus punctatus
Channel catfish (2.5 yr; 767 g, F,M
394 mm) ,
Ictalurus punctatus
Channel catfish (yolk sac fry; S,U
1-4 day).
Ictalurus punctatus
Channel catfish (swim-up fry; S,U
5-8 days old),
Ictalurus punctatus
Channel catf 1 sh (0.15 g) , F,U
Ictalurus punctatus
Channel catfish (0.5-1.5 g) , S,U
Ictalurus punctatus
Channel catfish (0.5-1.5 g) , S,U
1 ctal urus punctatus
Mosqultoflsh (0.32 g) , S,U
Gambusla afflnls
Mosqultoflsh (0.32 g) , S,U
Gambusla afflnls
Mosqultoflsh (0.32 g) , S,U
Gambusla afflnls
Mosqultoflsh (0.32 g) , S,U
ftambusla afflnis
Test
Material""
T
T
T
T
T
T
T
T
T
T
Floating
(10*)
Sinking
(62.6* )
Floating
(10*)
Sinking
(62.6*)
Te»perature LC5O or
TO ECSO (»g/L)*<">
20 (pH 8.2, 3.2ft
alk 220, hard 40)
20 (pH 8.2, 3.9tf
alk 220, hard 160)
20 (pH 8.2, 4.7tf
alk 220, hard 320)
4 20 (pH 7.4, 5.5tf
alk 237, hard 272)
20 16. 5tf
25 8«
25 0.8
25 (pH 7.4, 7.5n
alk 237, hard 272)
25 2.8n
25 (pH 7.4, 3.7tf
alk 35, hard 40)
20 (pH 8.3, 24
TOS 166)
20( pH 8.3, 48
TOS 166)
t
20( pH 7.8, 52
TOS 238)
20 (pH 7.8, 6
TOS 238)
Spec Us Mean
Acute Valve
(noA) Reference
Johnson and Jul In 1980
Johnson and Jul In 1980
Johnson and Jul In 1980
Johnson and Jul in 1980
Mayer et al . 1977
Johnson and Jul In 1980
Johnson and Jul in 1980
Johnson and Jul In 1980
Johnson and Jul In 1980
0.8 Johnson and Jul In 1980
Workman and Neuhold 1963
Workman and Neuhold 1963
Workman and Neuhold 1963
Workman and Neuhold 1963
-------
Species
Mosqultoflsh (0.32 g) ,
Gambusla afflnis
tosqultoflsh (0.32 g) ,
Gambusla afflnls
Mosqultoflsh (30-40 mm).
Gambusla afflnls
Guppy (0.1-0.2 g) ,
Poecllla retlculata
Striped bass (Juvenile; 2.3 g) ,
Morone saxatl 1 Is
Striped bass (56 days).
Morone saxat Ills
Green sun fish.
Lepomls cyanellus
Blueglll (0.6-1.5 g) ,
Lepomls macrochlrus
Blueglll (0.6-1.7 g) ,
Lepomls macrochlrus
Blueglll (0.6-1.5 g) ,
Lepomls macrochlrus
Blueglll (0.6-1.5 g).
Lepomls macrochlrus
Blueglll (0.6-1.5 g) ,
Lepomls macrochlrus
Blueglll (0.6-1.5 g) ,
Lepomls macrochlrus
Blueglll (0.5-1.5 g) ,
Lepomls macrochlrus
Blueglll (0.5-1.5 g) ,
Lepomls macrochlrus
Method*
S.U
s.u
-fU
s.u
F.U
S.U
s.u
s.u
s,u
s.u
s.u
F.U
s.u
s,u
F.U
Test
Material"
Floating
(10*)
Sinking
(62.6|)
-
-
T
T
T
T
T
T
T
T
T
T
T
Temperature
CO
20 (pH 7.0,
IDS 46)
4
20 (pH 7.0,
TDS 46)
24
25
17
20
18
12.7
18
18.3
20
20
23.8
25
25
Species Mean
LC50 or Acute Value
EC50 (i.g/L)"» CuflA)
9
9
8 15.68
20 20
4.4
5.4 4.874
13 13
3.2
18
2.6
2.6
4.7
2.4
2.4
3.4
Reference
Workman and Neuhold 1963
Workman and Neuhold 1963
Chaiyarach et al . 1975
Henderson et al . 1959
Korn and Earnest 1974
Palawskl et al . 1985
Johnson and Flnley 1980
Macek et al . 1969
Macek and McAllister 1970
Macek et al . 1969
Johnson and Jul In 1980
Johnson and Jul In 1980
Macek et al . 1969;
Johnson and Flnley 1980
Johnson and Ju! In 1930
Johnson and Jul In 1930
-------
u>
Tebla 1. (continued)
>L_4-hsw4*
Spacta* H«tfcoo_.
Blueglll (3.8-6.4 cm, S,U
1.0-2.0 g),
L epomls macrochlrus
Blueglll (3.8-6.4 on, S,U
1.0-2.0 g)
L epomls jnacrochlrus
Bluegill (3.8-6.4 cm, 1.0-2.0 g) , S,U
L epomls macrochlrus
Redear sun fish (0.6-1.7 g) , S,U
Lepomls mlcrolophus
Largemouth bass (0.9 g) , S,U
Mlcropterus sal mo Ides
Yellow perch (1.4 g) , s»u
Perca flavescens
Western chorus frog (tadpole, S,U
7 day).
Pseudacrls trlserlata
last
Matarlal**
T
EC
(20%)
EC
(20*)
T
T
T
1
Twperatur* LC50 or
(»C) EC50 (»aA)**"
25 3-5
(soft water)
25 . 4-6
(hard water)
IE 4 4
25 H*^
(soft water)
18 l5
1 O
18 2
18 12
15 5 500
1 ^« •*
_ • * r\
Sp«cl«s Naan
Acut* Val«*
3.822
13
2
12
500
i An
Fowler's toad (tadpole,
28-35 day),
Bufo fowlerl
S.U
15.5
Henderson et al. 1960
Henderson et al . 1960
Henderson et al. I960
Macek and McAllister 1970
Johnson and Flnley 1980
Johnson and Flnley 1980
Sanders 1970
Sanders 1970
-------
Table I. iconTinueoi
Species
Common rang la (adult),
Rang la cuneata
Qua hog clam (embryo).
Mercenar la mercenarla
Mysld (juvenile) ,
Mysldopsls bah la
Mysld (adult),
Mysldopsls bah la
Mysld (Juvenile),
Mysldopsls bah la
Mysld (Juvenile),
Mysldopsls bah la
u> Pink shrimp (nauplius).
*~ Penaeus duorarum
Pink shrimp ( protozoea) ,
Penaeus duorarum
Pink shr Imp (mysls) ,
Penaeus duorarum
Pink shr Ip (adult),
Penaeus duorarum
Korean shr Imp ( adult) ,
Pal aemon macrodacty 1 us
Korean shr Imp ( adult) ,
Pal aemon macrodacty 1 us
Grass shrimp (adult).
Palaemonetes pug Jo
Bl ue crab (adult) ,
Method*
S, U
R, U
F, M
F, M
F, M
F, M
s, u
S, U
S, U
F, M
S, U
F, U
F, M
S, U
Test ' Salinity LC50 or
Material** (fl/kfl) EC50 Uo/l)***
SALTWATER SPECIES
5 460,000
1 , 1 20
T 20-26 6.32
T 20-26 3.19
T - 2.67
T 30 2.05
(71.6$) - L575
(71.6$) - L288
(71.6$) - 1.002
T 23.9 1.4
t
T 27 20.3
T 26 20.8
T 21.3 ' 4.4
8.6 580
/ irt»r>>
Species Mean
Acute Value
(•0/L)
460,000
1,120
-
-
-
3.222
-
-
-
1.4
-
20.55
4.4
~
CalIInectes sapldus
Reference
Chalyarach et at. 1975
Davis and Hldu 1969
Nlmmo 1977
Nlmmo 1977
Nlmmo et al. 1981
Kuhn and Chammas 1986
Courtenay and Roberts 1973
Courtenay and Roberts 1973
Courtenay and Roberts 1973
Schlmmel et al . 1977
Earnest 1970
Earnest 1970
Schlmmel et al . 1977
Mahood et al . 1970;
McKenzle 1970
-------
Table 1. (continued)
MatKod*
Species H* ' -
Blue crab (adult), s» u
Call Inectes sapldus
Blue crab (adult), s» u
Call Inectes sapldus
Blue crab (adult), s» u
Cal I Inectes sapldus
Blue crab (adult), S, U
Call Inectes sapldus
Bl ue crab (adult), s» u
Call Inectes^ sapldus
Blue crab (adult), S, U
Call Inectes sapldus
C II
Blue crab (adult), S, U
Cal 1 Inectes sapldus
Blue crab (adult), S, U
Call Inectes sapldus
Mud crab (stage 1 larva), S, U
Rhlthropanopeus harrlsll
Drift line crab (stage II larva), S, U
Sesarma clnereum
Drift line crab (stage III larva), S, U
Sesarma cinereum
Drift line crab (stage IV larva), S, U
Sesarma clnereum
Drift line crab (megalopa), S, U
Species Mean
Test Salinity LC50 or Acute Value
8.6 900
(15*C)
8.6 370
(21 *C)
19.3 960
(10"C)
19.3 3,800
(15*C)
19.3 770
(21 *C)
24.2 1,200
(10*C)
24.2 2,700
(15*C)
24.2 1,000 1,065
(21 *C)
(71.60 - 3'-32 3K32
•
m/rrf \ — 0. 5442 —
.60 v/.v
(71.60 - °'5298
(71. 6O - 4<869
ft 014^ 0.5370
m£.ef\ • Oe"'™ ve-'-'*>*
.60 "•
Reference
Mahood et al. 1970;
McKenzle 1970
Mahood at al. 1970;
McKenzle 1970
Mahood et al. 1970;
McKenzle 1970
Mahood et al. 1970;
McKenzle 1970
Mahood et al. 1970;
McKenzle 1970
Mahood et al. 1970;
McKenzle 1970
Mahood et al. 1970;
McKenzle 1970
Mahood et al. 1970;
McKenzle 1970
Courtenay and Roberts 1973
Courtenay and Roberts 1973
Courtenay and Roberts 1973
Courtenay and Roberts 1973
Courtenay and Roberts 1973
Sesarma clnereum
-------
Table 1. (continued)
Species
Sheepshead minnow (juvenile).
Cyprlnodon varlegatus
Threespine stickleback (adult).
Gasterosteus aculeatus
Threespine stickleback (adult).
Gasterosteus aculeatus
Striped bass (Juvenile),
Morone saxat Ills
Striped bass (56 days).
Morone saxat Ills
Plnflsh (Juvenile),
Lagodon rhombo.des
Spot (Juvenile) ,
Lelostomus xanthurus
White mullet (Juvenile),
Mug II curetna
» S - static; R = renewal; F =
»* EC = emulslflable concentrate
Test
Method* Material**
F, M T
S, U
S, U
F, U T
S, U T
F, M T
F. M
F, M
Salinity
(0/kq)
23.2
5
25
30
I
I
22.5
32-35
1
32-35
Species Mean
LC50 or Acute Value
ECM (po/U*** (nq/L)
1.1 1.1
8.6
7.8 8.190
4.4
7.6 5.783
0.53 0.53
0.92 0.92
2.88 2.88
Reference
Schlmmel et al
Katz 1961
Katz 1961
. 1977
Korn and Earnest 1974
Palawskl et al
Schlmmel et al
Harder et al .
Harder et al .
. 1985
. 1977
1983
1983
flow-through; M = measured; U = unmeasured.
; CS = commercial stock.
probabl y an emul si
*_•__ _ ._ i ,^_ . _. i ^ A
flable concentrate; T » technical
«.k.» IA « l — i-i** «s4^ +svt/*nKAriA 1 *E lOOm.
grade. Percent
pur Ity
,f the concentrations -ere not measured and the published results were not reported to be adjusted for pcrlty. the published results
were multlpl led by the purity It It was reported to be less than 97*.
value Is inordinately different from others for this spec.es and therefore not used In calculation of Spec.es Kaan Acute Value.
Not used In calculation of Species Mean Acute Value because data are available for a more sensitive life stage.
-------
Table 2. Chronic Toxiclty of Toxaphan* to Aquatic AnlMls
Cn^M* 1 AC
3PSCi»
Cladoceran,
Daphnla magna
Brook trout,
Salvellnus fontlnalls
Fathead minnow.
Plmephales promelas
Channel catfish,
Ictalurus punctatus
T«st
T«st* Material**
LC T
LC T
LC T
LC T
Taapwatur*
(•C)
LlMltS
(,g/L)*««
Chronic Value
(na/L)
Reference
FRESHWATER SPECIES
18
9
25
26
0.07-0.12
<0.039*«»*
0.025-0.054
0.129-0.299
0.09165
<0.039
0.03674
0. 1964
Sanders 1980
Mayer and Me trie
Mayer et al . 1977
Mayer et al . 1977
1978
SALTWATER SPECIES
Mysld,
Mysldopsls bah la
Sheepshead minnow,
Cyprlnodon varleqatus
Sheepshead minnow.
Cyprlnodon varlegatus
Long nose Ml 1 If Ish,
Fundulus slml 1 Is
LC T
ELS T
LC T
ELS T
-
12.9*
(7-23.5)
7.5-32t
10.5-30t
1.585-2.03
1.1-2.5
0.51-1.0
<0.3*»»»
1.794
1.658
0.7141
<0.3
Kuhn and Ch aromas
1986
Goodman et al . 1976
Goodman 1986
Schlmmel et al .
1977
* LC = life-cycle or partial life-cycle; ELS « early life-stage.
'»• T = technical grade. Percent purity Is given In parentheses -hen available. * definition, the purity of technical-grade
toxaphene Is 100)1.
«** Results are based on measured concentrations of toxaphene.
**»* Unacceptable effects occurred at all concentrations tested,.
f Salinity (g/kg), not temperature.
-------
Table 2. (continued)
Acute-Chronic Ratio
Species
Cladoceran,
Daphnla magna
Fathead minnow.
Plmephales promelas
Channel catfish.
Ictalurus punctatus
Mysld,
Mysldopsls bah la
Sheepshead minnow.
Cvprlnodon varlegatus
Sheepshead minnow.
Cvprlnodon varlegatus
Acute Value
Uq/L
10
1.2
5.5*
2.03
1.1
1.1
Chronic Value
(iiq/L)
0.09165
0.03674
0.1964
1.794
1.658
0.7141
Ratio
109.1
196.0
28.00
1.132
0.6634
1.540**
CO
CO
* This acute value was measured with juveniles In the same water
that was used In the chronic test with this species.
»* This value takes precedence for this species because It Is based
on a life-cycle test, rather than an early life-stage test.
-------
Tabl* 3. Rank* G«"us NMA Acut. Valua «lth Sp«cl«* Nam Ac«t«-Chronlc Ratios
VD
Ganiik MMH Sp«cl«» •*••« Spacla* MMM
A^ vtlu. Ac«t« Valu« Acut«-Chro«lc
ACUT* vaiu* . . .M R.tlo***
lankm i..n/i> SMC«»» '
-------
Table 3. (continued)
Rank*
17
16
15
14
13
12
11
10
9
Genus Mean
Acute Value
(wa/L) Species
13.78 Cladoceran,
Stmocaphalus serrulatus
12.08 Cladoceran,
Oaphnla maqna
Cladocaran,
Daphnla pulex
12 Yel low perch,
Perca flavescens
<11.19 Central stoneroller,
Campostoma anomalum
10.95 Bluntnose minnow,
PImephales notatus
Fathead minnow,
P 1 mepha 1 as pr ome 1 as
10.8 Brook trout,
Salvellnus fontlnalls
8.644 Green sun fish,
Lepomts cyanellus
Blueglll,
Leporols macrochlrus
Red ear sun fish,
Lepomls mlcrolophus
<5.477 Golden shiner,
Notemlqonus crysoteucas
4.874 Striped bass.
Species HMD
Acute Value
13.78
10
14.59
12
11.85
10.12
10.8
13
3.822
13
<5.477
4.874
Species New
Acute-Chronic
Ratio""
109.1
196.0
Morone saxatlI Is
-------
Table 3. (continued)
Rank*
«MW«*^B-»
8
7
6
5
4
3
2
1
15
14
Genus MMUI opw*.«"» — ™
Acute Value ^l^n/i %•*
4.234 Rainbow trout, 5.782
Salmo qalrdnerl
Brown trout, 3-'
Salmo trutta
3.7 Common carp, 3>'
Cyprlnus carplo
3.626 Coho salmon, 6-7
Oncorhynchus klsutch
Chinook salmon, '«962
Oncorhynchus tshawytscha
3.0 Stonefly, 3'°
Pteronarcel la bad I a
2.3 Stonefly, 2'3
Pteronarcys callfornlca
2 Largemouth bass, 2
Mlcropterus sal mo Ides
1.660 Black bullhead, 3.446
Ictalurus me I as
Channel catfish, °-8
Ictalurus punctatus
1.3 Stonefly, ''3
Claassenla sabutosa
SALTWATER SPECIES
460,000 Common rang la, ' 460,000
Ran£la cuneata
1,120 Quahog clam, '.12°
Mercenarta mercenarla
Acute-Chronic
Ratio*"
28.00
-------
Table 3. (continued)
Rank*
13
12
11
10
9
8
7
6
5
4
3
Genus Mean
Acute Value
(pfl/L)
1,065
31.32
20.55
8.190
5.783
4.4
3.222
2.88
1.4
1.1
0.92
Species
Bl ue crab,
Cal 1 Inectes sapldus
Mud crab,
Rhlthropaneopeus harrlsH
Korean shr Imp,
Palaemon macrodacty 1 us
Threesplne stickleback,
Gasterosteus aculeatus
Striped bass,
Morone saxatll Is
Grass shr Imp,
Palaemonetes puglo
Mys Id ,
Hysldopsls bah la
White mul let.
Mug 11 curema
Pink shrimp,
Penaeus duorarum
Sheepshead minnow,
Cyprlnodon varleqatus
Spot,
Species Mean
Acute Value
(i.a/L)*»
1,065
31.32
20.55
8.190
5.783
4.4
3.222
2.88
1.4
1.1
0.92
Species Mean
Acute-Chronic
Ratlo»»«
1.132
1.540
-------
Table 3. (continued)
6wius N»an
Acute Value
0.5370
Species
Drift I Ine crab,
Sesarma clnereure
0.53
PInflsh,
Laqodon rhomboldes
Value Is not unnecessarily lowered.
«» From Table 1.
*»* From Table 2.
Species Mean
Acute Value
(.q/L)**
0.5370
0.53
Species Mean
Acute-Chronic
Ratio***
Fresh water
Final Acute Value = 1.467 M9/L
Criterion Maxima Concentration = (1.467 MoA> / 2 = 0.7335 Mg/L
Final Chronic Value = <0.039 Mg/L (to protect brook trout; see text)
Salt water
Final Acute Value = 0.4197 Mg/L
Crlterion Maxlmun Concentration = (0.4197 Mo/L> / 2 = 0.2098 ,g/l
Final Acute-Chronic Ratio * 2 (see text)
Final Chronic Value.= (0.4197 pg/L) /2 =0.2098
-------
TabU 4. Toxic I ty at Toxaph«n« to Aquatic Plant*
Green alga,
Scenedesmus quadrlcauda
- ' -
Green alga,
Salenastrum caprlcornutum
2)
24
FRESHWATER SPECJES.
,0 Significant decrease 100-1,000 Stadnyk et al . 1971
In cell numbers
4 EC50 (reduced growth) 380 Cal I et al . 1983
. .n
were multiplied by the purity If It was reported to be less than 97J.
-------
Table 5. Bloaccimilatlon of Toxaph««« by Aquatic Organ Is-*
T«st
_ • Material*
Specie* HCTW iai
-r
Cladoceran, '
Daphnla magna
Brook trout, T
Salvellnus fontlnalls
Brook trout, T
Salvellnus fontlnalls
Brook trout, T
Sjalvellnus tontlnalls
Brook trout, T
Salvellnus fontlnalls
Brook trout, T
Salvellnus fontlnalls
Brook trout, T
Salvellnus fontlnalls
Fathead minnow, T
PI mephales promelas
Fathead minnow, T
PI mephales promelas
Fathead minnow, T
Plmephales promelas
Fathead minnow, T
Plmephales promelas
Fathead minnow, T
Plmephales promelas
Channel catfish, T
Ictalurus punctatus
Channel catfish, T
Ictalurus punctatus
Concentration
In Water (i.q/L)""
0.06-0. 12
0.039-0.139
0.068-0.502
0.039-0.139
0.059-0.502
0.039-0.502
0.068-0.502
0.013-0.173
0.013-0.173
0.013-0.173
0.055-0.621
0.013-0.173
0.049-0.630
0.049-0.630
Duration
(days)
FRESHWATER
7
60
60
90
140
161
161
30
30
98
150
295
30
30
Percent
Tissue Hold*
SPECIES
Whole
body
Whole
body
vw J
Who 1 e
body
V W f
Whole
bodv
ISVXW J
Whole
bodv
ww J
Whole
bodv
V w 7
Fillet
Whole 5.2
body
Whole 5.7
body
Whole 9.3
body
Whole
body
Whole 2.7
body
Whole ' 1.8
body
Whole 8.8
body
BCF or NonMllz«d
BAF«»« BCF or BAFT
4 Ann ~
y UUU
12,000
4 200 ~
18,000
9,400
6 400 ~
3,100
16,000 3,077
22,000 3,860
51,000 5,484
f\f\ f\f\(\ ~
90,000
7,900 2,926
11,000 6,111
13,000 1,477
Reference
^—^"^^•™l^^^— *™
Sanders 1980
Mayer et at .
1975
Mayer et al .
1975
Mayer et al .
1975
Mayer et al .
1975
Mayer et al .
1975
Mayer et al .
1975
Mayer et al .
1977
Mayer et al .
1977
Mayer et al .
1977
Mehrle and
Mayer 1975
Mayer et al .
1977
Mayer et al .
1977
Mayer et al ,
1977
-------
Table 5. (continued)
Test
C-^^IA* Material"
Channel catfish, T
Ictalurus punctatus
Channel catfish, T
tctaiurus punctatus^
Channel catfish, T
Ictalurus punctatus
Channel catfish, T
Ictalurus punctatus^
Channel catfish, T
Ictalurus^ punctatus
Eastern oyster (juvenile T
to adult).
Crassostrea virgin lea
Sheepshead minnow T
(juvenile).
Cyprlnodon varlegatus
Sheepshead minnow T
(juvenile, first
generation) ,
Cyprlnodon varlegatus
Sheepshead minnow T
(Juvenile, second
generation) ,
Cyprlnodon varlegatus
Sheepshead minnow T
(adult female),
Cyprinodon varlegatus
Sheepshead minnow T
(adult male) ,
Cyprlnodon varlegatus
Concentration
ia Mater (»o/L)«*
0.049-0.630
0.049-0.630
0.049-0.630
0.049-0.630
0.049-0.630
0.7-0.8
0.20-2.5
0.28-0.51 '
0.28-1.0
0.28-1.0
0.28-UO
Duration Percent
(days) Tissue Llplds
50 Whole 8.2
Ksvl \t
DOQy
60 Whole 2.7
body
75 Whole 7.1
K^v( it
Dooy
90 Whole 4.7
bod y
100 Whole 7.6
body
SALTWATER SPECIES
84, 168, Edible
252 tissue
28 Whole 3.2ft
body
35 Whole 3.2ft
body
35 Whole 3.2n
Si-vi\j
UIAJ y
155, 183 Whole 4.1ttf
body
155, 183 Whole 3.2ttf
body
BCF or NorMallzed
BAF**" BCF or BAFT
12,000 1,463
24,000 8,889
18,000 2,535
39,000 8,298
22,000 2,895
13,350
(2)
9 380 2,931
2
-------
Table 5. (continued)
Species
Test
Material*
Concentration Duration
In Mater Ug/L)*" (days) Tissue
Percent
LlDlds
BCF or
BAF«»
Normalized.
BCF or BAF* Reference
Longnose kllllflsh
(embryo, fry),
Fundulus slml.Ms,
Longnose kllllflsh (fry),
Fundulus sltnl Ms
Longnose kllllflsh
(Juvenile),
Fundulus slmllls
Longnose kllllflsh (ovun),
Fundulus slmllls
T
T
0.3-1.3
0.3-1.4
0.3-1.7
0.2-0.9
28
28
28
32
Whole
body
Whole
body
Whole
body
Ova
l.2
ftt
<.2
ftt
1.2
tn
3,^0
34^0
3,408
(3)
18'870
26,290
26,290
Schlmmel et al .
Schlmmel et al
Schjmmel et aI
Schlmmel et al
1977
• T - technical grade. Percent purity Is given In parentheses -hen available. By definition, the purity of technlea,-grade toxaphene „
100*.
** Measured concentration of toxaphene.
of
In
of exposure concentrations from whicn me geomejrit moan «**^ — -- -
greater than 1.
t When possible, the factors -ere norma.lzed to 1* llpld. by dividing the BCFs and BAFs by the percent Mplds.
tt
ttt
From Moore (1981).
From Hansen (1980).
Maximum Permissible Tls«ue Concentration
Consumer
Man
• Action Level or Effect
Action level for edible
fish or shell fish
Concentration
(•a/kg)
Reference
U.S. FDA 1985
-------
TabU 5. (continued)
Geometric mean normalized BCF = 6,195
Fresh water
Highest percent llplds In edible portion of
commonly consuned species = II (Stephan et at. 1985)
Final Residue Value = (5 tng/kg) / (6,195 x II) = 0.00007337 mg/kg
= 0.07337 ng/L
See text concerning field data.
j>att water
Highest percent llplds In edible portion of
commonly consumed species = 10 (Stephan et al. 1985)
Final Residue Value = (5 mo/kg) / (6,195 x 10) = 0.00008071 mg/kg
= 0.08071 |ig/L
oo See text concerning field data.
-------
Tab.. 6. Otl~ D.ta on Etfct. of Tox..n««. on Aquatic Org.nl-.
Concentration
T*st
vo
SH.CU.
Cladoceran,
Daphnla magna
Cladoceran (1st Instar,
<24 hr).
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Isopod,
Asellus Intermedlus
Am phi pod.
Gammarus fasclatuA
Amphlpod (15-20 mm),
GammaruA fasclatus
Amphlpod (5-10 day old).
Gammarus. fasclatus
Pr awn ,
Pjilaamonetes kadlakensls
Prawn ,
Pa.aemonetes kadlakensls
Prawn ,
Palaemonetes kadlakensls
Prawn ,
P«i/uimonetes kadlakensls
Prawn f
Palaemonetes kadlakensls
Prawn ,
Palaemonetes kadlakensls
Mff+~l.l* CO ._ UUT.T,™ ^i_^
FRESHWATER SPECIES
EC ,2.7 24 hr LC50
,9 26 hr UC50
0,1 26 hr EC50
R /l*1 (Immobilization)
o* 26 hr EC50
R *-' (Immobilization)
12.7 24 hr U50
12.7 24 hr LC50
CX*
7.67 hr LT50
T
,Q 30 day Reduced growth
T '
74 24 hr LC50
T - 24 (Site 1)
24 24 hr UC50
T l* (Site 2)
24 24 hr LC50
T ZA (Site 3)
94 24 hr LC50
T . (Site 4)
on 36 hr LC50
T 20 3 (Site 1)
20 36 hr LC50
T /u (Site 2)
1,500
94
260
1,900
100
60
\J\J
50
0.18
44
229
20.9
80.9
170
57.5
Hooper and Grzenda 1955
Frear and Boyd 1967
Crosby et al. 1966
Crosby et al. 1966
Hooper and Grzenda 1955
Hooper and Grzenda 1955
McDonald 1962
Sanders 1980
Naqvl and Ferguson 1970
Naqvl and Ferguson 1970
Naqvl and Ferguson 1970
Naqvl and Ferguson 1970
Ferguson et al. 1965a
Ferguson et al . 1965a
-------
Table 6. (continued)
Test
* «— Material*
Species . - —
White River crayfish (0.25- T
0.40 g; 11.8-14.6 mm),
Procambarus acutus
White River crayfish (0.25- T
0.40 g; 11.8-14.6 mm).
Procambarus acutus
Mayfly, EC
Ephemera slmulans
Mosquito (larva, 2nd Instar),
Aedes aegyptl
Mosquito (larva, 4th Instar), T
Aedes aegyptl
Mosquito (larva, 4th Instar), T
Aedes aegyptl
Mosquito (larva, 4th Instar), T
Aedes aegyptl
Mosquito (larva, 4th Instar), T
Aedes aegyptl
Rainbow trout, ^Vup )•
Salmo jalrdnerj and WK l
T
Brook trout ( embryo) , '
Salve) Inus fontlnalls
Brook trout (133 g; 231 mm), T
Salvellnus fontlnal Is
Stoneroller, cs
Campostoma anomalum
Temperature
(»C> Duration
- 48 hr
_ 48 nr
12.7 24 hr
>5 hr
24 hr
21-23 48 hr
21-23 48 hr
21-23 48 hr
24 hr
rrtrf \
>0> )
9 90 day
post hatch
10 8 day
22 7 48 hr
fc*- • * 1
20 24 hr
ooocvn 1 1 • i IWM
Effect Ua/L>M
EC50 60.7
( Immobilization)
EC50 90.2
( Immobilization)
LC50 9,500
ET50 10
( Immobilization)
LC50 375.5
LC50 1,900
(Site 1)
UC50 > 81 ,920
(Site 2)
UC50 140
(Site 3)
LC50 <50
Disrupted ver- 0.039
tebrae collagen
metabolism
LC50 4.9
l£50 8
LC50 20
Reference
Albaugh 1972
Albaugh 1972
Hooper and Grzenda 1955
Burch field and Storrs 1954
Chandurkar et al . 1978
Klassen et al . 1965
Klassen et al . 1965
Klassen et al . 1965
Mayhew 1955
Mehrle and Mayer 1975a
Mayer et al . 1975
kl u.>4 t 1 Qfi A
Mahdl 19oo
Turner et al . 1977
Goldfish,
Carasslus auratus
-------
Table 6. (continued)
sp~f*»
Goldfish (6 cm),
Harass 1 us auratus
Golden shiner,
Notemlgonus crysoleucas
Golden shiner,
Notemlqonus crysoleucas
Golden shiner,
Notemlqonus crysoleucas
Golden shiner,
Noterolqonus crysoleucas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow (3-3.5 cm),
Plmephales promelas
Fathead minnow (30 day; 0.32
g; 30 mm),
Plmephales promelas
Fathead minnow (0.5-1.5 g),
Plmephales promelas
Fathead minnow (10 day old),
Plmephales promelas
Fathead minnow (0.5-1.5 g),
Plmephales promelas
Black bullhead (fIngerlIng),
Ictalurus melas
Black bullhead ( finger I Ing),
Ictalurus melas
Test
Material*
CS
T
T .
CS
EC
EC
_
T
T
T
T
T
T
Temperature
(*C> Pur at Ion
25 96 hr
11.7 24 hr
20 36 hr
20 36 hr
17.2 72 hr
10 24 hr
23.8 24 hr
48 hr
25 10 day
25 16 day
25 150 day
20 24 day
20 36 hr '
20 36 hr
Concentration
Affected 0.44
behav lor
LC50 12.5
UC50 30
(Site 1)
UC50 1200
(Site 2)
LC50 6.2
LC50 36
UC50 5.7
LC50 77.55
LC50 4.8
LC50 1.5
Impaired bone 0.054
quality
LC50 2.6
UC50 12.5
(Site 1)
UC50 50
(Site 2)
Reference
Warner et
Mahdl 196C
Ferguson
Ferguson
Mahdl 196i
Hooper an
Hooper ar
Chandurkj
Mayer et
Johnson
Mehrle a
Johnson
Fergusor
Fergusor
-------
Table 6. (continued)
Test
Black bullhead ( f tngerl Ing) , T
Ictalurus melas
Black bullhead (tingerl Ing) , T
Ictalurus melas
Channel catfish ( tingerl Ing, T
0.5-1.5 g).
Ictalurus punctatus
Channel cattish (0.15 g), T
Ictalurus punctatus
Channel catfish (4 g), T
Ictalurus punctatus
Channel catfish (2.5 yr; 767 T
g, 394 mm) ,
1 eta 1 urus punctatus
Channel catfish, T
Ictalurus punctatus
Mosqultof Ish,
Gambusla afflnls
Mosqultof Ish,
Gambusla afflnls
Mosquito fish.
Gambusla afflnls
Mosqultof Ish,
Gambusla afflnls
Mosquito fish.
Gambusla afflnl^
Mosqultof Ish.
Gambusla afflnls
Mosqultof Ish,
Temper ature
CO
20
20
15
25
20
20
20
20
£ \J
90
i. VJ
20
ff\l
90
i. \f
20
20
20
Duration
36 hr
36 hr
24 hr
12 day
29 day
9 day
90 day
36 hr
36 hr
36 hr
36 hr
36 hr
1
36 hr
36 hr
Effect
LC50
(Site 3)
LC50
(Site 4)
LC50
LC50
LC50
LC50
Impa Ired
bone qua!
LC50
(Site 1)
LC50
(Site 2)
LC50
(Site 3)
LC50
(Site 4)
LC50
(Site 5)
LC50
(Sits 6)
LC50
(Site 7)
Concentration
Uo/L)**
3.75
22.5
12.5
3.7
1.9
15
0.072
Ity
10
30
25
<10
20
15
>200
Reference
Ferguson et al . 1965b
Ferguson et al . 1965b
Johnson and Julln 1980
Johnson and Julln 1980
Johnson and Julln 1980
Mayer et al . 1977
Mayer et al . 1977
Ferguson et al . 1965b
Ferguson et al . 1965b
Ferugson et al . I965b
Ferguson et al . 1965b
Ferugson et al . I965b
Ferguson et al . 1963b
Ferguson et al . I965b
Gambusla afflnls
-------
TabI* 6. (continued)
:les
Mosqultoflsh (adult),
Gambusla afflnls
Mosqultoflsh (adult),
Gambusla afflnls
Mosqultoflsh (adult),
Gambusla afflnls
Mosqultoflsh (adult),
Gambusla jfflnls
Mosqultoflsh,
Gambusla afflnls
Mosqultoflsh,
Gambusla afflnls
Mosqultoflsh,
Gambusla afflnls
Mosqultoflsh,
Gambusla afflnls
BI ueg 111,
Lepomls macrochlrus
Blueglll (6-10 cm),
Lepomls macrochlrus
Blueglll (0.5-1.5 g),
Lepomls reacrochlrus
Bullfrog (larva),
Rana catesbelana
Leopard frog (embryo),
Rana sphenocephaI a
Leopard frog (young larva),
Rana sphenocephaI a
Test
IA*+aV 1 A 1 *
nvim •••
T
T
T
-
-
-
T
T
T
T
T
T
T
Temperature
(•C) Duration
21.1 36 hr
21.1 36 hr
21.1 36 hr
21.1 36 hr
48 hr
48 hr
48 hr
15 mtn
20.5 72 hr
19.2-20.5 21 and 42
20 34 day
96 hr
20 96 hr
20 96 hr
Concentration
LC50 10
(Site 1)
LC50 160
(Site 2)
LC50 60
(Site 3)
LC50 480
(Site 4)
LC50 31
(Site 1)
LC50 212
(Site 2)
LC50 301
(Site 3)
Avoidance 250
LC50 1.5
day Reduced cyto- 0.144
chrome P-450
activity levels
LC50 O.7
LC50 (after 99
8 days)
LC50 (after 46
24 days)
LC50 (after 32
30 days)
Reference
Boyd and F
Boyd and 1
Boyd and !
Boyd and
Dzluk and
Dzluk and
Dzluk and
Kynard 1?
Auwarter
Auwarter
Johnson
Hal 1 and
Hal 1 anc
Hal 1 anc
1977
-------
Table 6. (continued)
Species
Leopard frog (sub- adult),
Rana sphenocephala
Wood frog ( larva),
Rana sylvatlca
American toad ( larva),
Bufo amer lean us
Northern cricket frog.
( larva).
Acrls crepltans
Spotted salamander (larva).
Ambystoma roaculatum
Marbled salamander (larva).
Ambystoma opacum
Natural phy to plankton
communities
Green alga,
Protococcus sp.
Green alga,
Dunallella euchlora
Green alga,
Chlorella sp.
Golden-brown alga,
Monocrysls lutherl
Diatom,
Phaeodactvlum trlcornutum
Protozoan,
Euplotes sp.
Test Temperature
Material* (*C> Duration
T
T
T
—
EC
(60*)
EC
(60*)
EC
(60*)
EC
(60*)
•
(60*)
20 96 hr
96 hr
96 hr
96 hr
96 hr
96 hr
SALTWATER SPECIES
- 4 hr
10 days
10 days
10 days
10 days
10 days
24 hr .
Concentration
Effect Ua/L)**
LC50 (after 378
8 days)
LC50 (after 195
8 days)
LC50 (after 34
8 days)
l£50 (after 76
8 days)
l£50 (after 34
8 days)
LC50 (after 342
8 days)
90.8* de- 1,000
crease In
23* reduction 40
In growth
45* reduction 40
In growth
30* reduction 10-40
In growth
22% reduction 0.015
In growth
46* reduction 10
In growth
EC50 (re- 1,250***
duced growth)
Reference
Hal 1 and Swlneford
Hal 1 and Swtneford
Hal 1 and Swlneford
Hal 1 and Swlneford
Hal 1 and Swlneford
Hal 1 and Swlneford
Butler 1963
Ukeles 1962
Ukeles 1962
Ukeles 1962
Ukeles 1962
Ukeles 1962
Weber et al . 1982
1980
1980
1981
1981
1981
1981
-------
Tabla 6. (continued)
Ui
Spacta*
Benthlc macrofauna
Test
Material*
Temperature
<»C) Duration
Concentration
Effect
Benthlc macrofauna
Eastern oyster (juvenile),
Crassostrea virgin lea
Eastern oyster (Juvenile),
Crassostrea vlrglnlca
Eastern oyster (juvenile),
Crassostrea vlrglnlca
Eastern oyster (juvenile),
Crassostrea vlrglnlca
Eastern oyster (Juvenile),
Crassostrea vlrglnlca
Qua hog clam (larva),
Mercenarla mercenarla
T
T
3 mo
3 mo
96 hr
96 hr
96 hr
9 mo
96 hr
12 days
Stgntflant It
reduction In
abundance and
number of
species of
arthropods;
significant
Increase In
abundance of
annel Ids and
moI(uses
to significant 0.77
effects on
faun at numbers
or diversity
EC50 (shell 34
deposition)
EC50 (shell 38
deposition)
EC50 (shell 16
deposition)
No significant 0.7
effect on
growth or
histology
BCF - 11,000
(4)t
LC50 <250
Reference
Hansen and Tagatz 1980
Han sen and Tagatz 1980
Butler 1963; U.S. Bureau
of Commercial Fisheries
1965
Butler 1963; Lowe at al.
1970; U.S. Bureau of
Commercial Fisheries
Sen Unmet at al. 1977
Lowe et al. 1971
Schtmmel at al. 1977
Davis and Hldu 1969
-------
Table 6. (continued)
Test
Material*
Temperature
(«C) Duration
Effect
Concentration
(»q/L)*«
Ln
Mysld,
Mysldopsls bah Ia
Brown shrimp (JuvenMe),
Penaeus aztecus
Pink shrimp (juvenile),
Penaeus duorarum
Pink shrimp (adult),
Penaeus duorarum
Grass shr Imp (Juven Me),
Palaemonetes pug to
Grass shrimp (adult),
Palaemonetes puglo
Crab (juvenile),
CallInectes ornatus
Blue crab (staqe I larva),
CallInectes sapldus
Blue crab (stage II larva),
nailInectes sapldus
Mud crab (larva),
Rhlthropanopeus harrlsIL
Drift IIne crab (larva),
Sesarma clnereum
Sand dollar (ambryo),
Echlnarachnlus parma
T
T
T
T
71.6*
71.6*
71 .6%
71.6*
14 days
28 hr
48 hr
84* decrease 0.14
In number of
young produced
EC50 (mortal- 2.7
Ity and loss
of equll Ibrlum)
EC50 (mortal- 4.2
II Ity and loss
of equllIbrlum)
96 hr
48 hr
96 hr
48 hr
96 hr
96 hr
96 hr
96 hr
1
3 days
BCF - 526.4
EC50 (mortal-
II Ity and loss
of equll Ibrlum)
BCF = 948.6
EC50 (mortal-
ity and loss
of equll Ibrlum)
Hlstolog leal
changes
No hlstolog H
cal changes
Hlstolog leal
changes
Hlstolog leal
changes
Arrested
development
(at prism
stage)
5.2
-
180
0.0072ft
0.0004tf
7'16°tt
U3.2TT
0.0215-
0.0286
10,000
Reference
Nlmmo et al . 1981;
Nlmmo 1977
U.S. Bureau of Commercial
Fisheries 1965; Lowe
et al. 1970; Butler 1963
U.S. Bureau of Commercial
Fisheries 1967; Lowe
et al. 1970
Schlmmel et al. 1977
U.S. Bureau of Commercial
Fisheries 1967
Schlmmel et al. 1977
U.S. Bureau of Commercial
Fisheries 1965; Butler
1963
Courtenay and Roberts
1973
Courtenay and Roberts
1973
Courtenay and Roberts
1973
Courtenay and Roberts
1973
Crawford and Guarlna
1976
-------
TabU 6. (continued)
Ln
Concentration
TMt Tamparatvra
u 4.11 t.i* <*C) Duration
Species Matarial* * Uf .
_ 95 hr
Sheepshead minnow (Juvenile), T
Cyrplnodon varlegatus
_ 24 hr
Longnose kllllflsh, T
Fundulus stmllls
48 hr
Longnose kllllflsh (juvenile).
Fundulus stmll Is
T -28 days
Longnose kllllflsh (fry), '
Fundulus slmllls
_ 28 days
Longnose kllllflsh (Juvenile), T
Fundulus stmllls
2 hr
Longnose kllllflsh (gamete), T
Fundulus slmllls
14 days
Longnose kllllflsh (adult), T
Fundulus slmtlls
"~ T _ 96 hr
Plnflsh (juvenile), '
Laqodon rhomboldes
48 hr
Spot (Juvenile),
i alostomus xanthurus '
T _ 144 hr
Spot (juvenile) ,
Lelostomus xanthurus
Spot (juvenile), T
Lelostomus xanthurus
T . 48 hr
Spot (Juvenile),
i alostomus xanthurus
' • 96 hr i
Spot (juvenile), "Parent
Lelostomus xanthurus toxaphene"
Eftact (po/D"
BCF = 4,284
(4)'
LC50 *B
LC50 28
_ 1 T
LC50 >«3
LC50 O-9
No effect on 0.32-10.0
fertilization
BCF - 5,329
(3)f
BCF - 3,850
(2)T
n
LC50 '«u
50* mortality 0.5
No effect on 0.01-0.1
growth or
survival
LC50 *•*•
BCF - 2,508
(3)f
Referanca
Schlmmel et al . 1977
U.S. Bureau of Commercial
Fisheries 1965
Lowe et al . 1970
Schlmmel et al . 1977
Schlmmel et al . 1977
Schlmmel et al . 1977
Schlmmel et al . 1977
Schlmmel et al . 1977
Butler 1964
Lowe 1964
Lowe 1964
U.S. Bureau of Commerc 1 a 1
Fisheries 1965
Harder et al . 1983
-------
Tab)* 6. (continued)
Specie*
Spot (juvenile),
Lelostomus xanthurus
Spot (Juvenile),
Lelostomus xanthurus
Striped mullet (juvenile),
Mug 11 cephalus
White mullet (Juvenile),
Mug 11 curema
White mullet (juvenile).
Mug 11 curema
White mullet (juvenile),
Mugll curema
Test
Material*
"Sed Iment-
degraded
toxaphene"
'•Sed Iment-
degraded
toxaphene"
"Parent
toxaphene"
"Sediment-
degraded
toxaphene"
"Sediment5-
degraded
toxaphene"
Temperature
(*C) Duration
96 hr
96 hr
48 hr
96 hr
96 hr
96 hr
Effect
BCF = 3,786
(3)f
l£50
LC50
BCF = 4,807
(4)*
BCF - 5,020
(2)T
L£50
Concentration
<»g/L)** Reference
Harder et al. 1983
1.10 Harder et al. 1983
3.2 Butler 1963; U.S. Bureau
of Commercial Fisheries
1965
Harder at al. 1983
Harder et al. 1983
1.02 Harder et al. 1983
» T =• technical grade; EC = emulslflable concentrate; R = refined commercial grade; WP = wettable powder; CS = commercial stock,
probably an Lul si flable concentrate. Percent purity Is given > parentheses when available. By definition, the purity of
technical-grade toxaphene Is lOOf.
»» If the concentrations were not measured and the published results were not reported to be adjusted for purity, the published results
were multiplied by the purity If It was reported to be less tan 91%.
«»» Value was obtained graphically.
f Number of exposure concentrations from which the geometric mean factor was calculated.
tf concentration adjusted to u9 toxaphene/L.
-------
REFERENCES
Acie, C. and E.L. Par*e. 1981. Pesticide u3e on major crop, in the north
central region. 1978. Research Bulletin 1132. Ohio Agricultural Research
and Development Center.
Albaugh, D.W. 1972. Insecticide tolerances of two crayfish population,
acutus) in south-central Texas. BuU . Environ. Contam. t«ic.l.
8:334-338.
4pplegate, V.C., J.H. HoweU , A.E. Hall, Jr. and M.A. Smith. 1957. Toxicity
o£ 4,346 chemicals to larval lampreys and fishes. Special Scientific Report -
Fisheries No. 207. U.S. Fish and Wildlife Service, Washington, DC.
Auwarter, A.G. 1977. So,, effects of toxaphene-methyl parathion interaction
on Muegill sunfish (Lep^is Hcrochi- Rafi»esque) . Ph.D. the.is. diversity
al Georgia, Athens, GA. Available fro.: diversity Microfilms, Ann Arbor, MI.
Order No. 77-29,738.
Ballsch.iter, K. , H. Buchert , S. Bihler and M. Zell. 1981. Baseline studies
of global pollution. IV. The pattern of pollution by organochlorine co.pounds_
in the North Atlantic as accumulated by fish. Fre3.niu3 Z. Anal. Chem.
306:323-339.
Bidleman, T.F. and G.E. Olney. 1975. Long range transport of toxaphene
insecticide in the atmosphere of the western North Atlantic. Nature 257:475-
477.
Blus, L.J.. T. Joanen, A.A. Belisle and R.H. Prouty. 1975. The brown pelican
and certain environmental pollutants in LouisUaa. Bull. Environ. Contam.
Toxicol. 13:646-655.
59
-------
Blus, L., E. Cromartie, L. McNease and T. Joanen. 1979a. Brown pelican:
Population status, reproductive success, and organochlorine residues in
Louisiana, 1971-1976. Bull. Environ. Contam. Toxicol. 22:128-135.
Blus, L.J., T.G. Lament and B.S. Neely, Jr. 1979b. Effects of organochlorine
residues on eggshell thickness, reproduction, and population status of
brown pelicans (Pelecanus occidentalis) in South Carolina and Florida, 1969-
76. Pestic. Monit. J. 12:172-184.
Boyd, C.E. 1964. Insecticides cause mosquitofish to abort. Prog. Fish-Cult.
26:138.
Boyd, C.E. and D.E. Ferguson. 1964. Susceptibility and resistance of
mosquitofish to several insecticides. J. Econ. Entomol. 57:430-431.
Bringmann, G. and R. Kuhn. 1960. The water-toxicological detection o-f
insecticides. Gesund.-Ing. 81:243-244.
Buhler D.R., R.R. Claeys and B.R. Mate. 1975. Heavy metal and chlorinated
hydrocarbon residues in California sea lions (Zalophus californianus
californianus). J. Fish. Res'. Board Can. 32:2391-2397.
Burchfield, H.P. and E.E. Storrs. 1954. Kinetics of insecticidal action
based on the photomigration of larvae of Aedes aegypti (L.) Contrib. Boyce
Thompson Inst. 17:439-452.
Burke, W.D. and D.E. Ferguson. 1969. Toxicities of four insecticides to
resistant and susceptible mosquitofish in static and flowing solutions.
Mosq. News 29:96-100.
60
-------
Sutler, P.*- »«3. Co-ercUl Aeries initiations, in: Pesticide-
uildlil. .tudi... A revie. .. «* »* «»««« ""l" I""'1""""
„„-«. Circuur 1". U.S. «.h and Wildlife Service, «asnington, 00. pp.
11-26.
Butler,
and ,«««.
during eh. „!«-„ ye«. r »,. U.S. n,H and WiUllf.
Washington, DC. pp. 5-28.
• c- ^ »{i
-------
Carter, R.L. and J.B. Graves. 1972. Measuring effects of insecticides on
aquatic animals. La. Agric. 16:14-15.
Casida, J.E., R.L. Holmstead, S. Khalifa, J.R. Knox, T. Ohsawa, K.J. Palmer
and R.Y. Wong. 1974. Toxaphene insecticide: A complex biodegradable mixture.
Science 183:520-521.
Chaiyarach, S., V. Ratananun and R.C. H.rrell. 1975. Acute toxicity of the
insecticides toxaphene and carbaryl and the herbicides propanil and molinate to
four species of aquatic organisms. Bull. Environ. Contain. Toxicol. 14:281-284.
Chandurkar, P.S. and F. Matsumura. 1979. Metabolism of toxicant B and
toxicant C of toxaphene in rats. Bull. Environ. Contam. Toxicol. 21:539-547.
Chandurkar, P.S., F. Matsumura and T. Ikeda. 1978. Identification and toxi-
city of toxicant Ac, a toxic'component of toxaphene. Chemosphere 7:123-130.
Clark, J.R., D. Devault, R.J. Bowden and J.A. Weishaar. 1984. Contaminant analysis
of fillets from Great Lakes coho salmon, 1980. J. Great Lakes Res. 10:38-47.
Cohen, D.B., G.W. Bowes and S.M. Ali. 1982. Toxaphene. Special Projects
Report No. 82-4SP. Toxic Substances Control Program, California State Water
Resources Control Board, Eureka, CA.
Cohen, J.M., L.J. Kamphake, A.E. Lemke, C. Henderson and R.L. Woodword.
I960. Effect of fish poisons on water supplies. Part 1. Removal of toxic
materials J. Am. Water Works Assoc. 52:1551-1566.
Cope, O.B. 1964. Sport fishery investigations. In: The effects of pesticides
on fish and wildlife. Circular No. 226. U.S. Fish and Wildlife Service,
Washington, DC. pp. 51-63.
62
-------
Courtenay, W.R., Jr. and *.H. -berts, Jr. 1973. Environmental effect, on
toxaphene toxicity to selected «*•• - <« '"->-»-«>•
National Technical Information Service, Springfield, VA.
Crawford, .... and A.M. Guarino. 1976. Sand dollar embryos as monitors of
environmental pollutants. Bull. Ht . Desert 1.1. Biol. Lab. 16:17.
Crockett, ..... = .B. »i«~. •• T.i - «•
Eish, vildlife, and est.arie,. Pestic. Monit. J. 8:235-240.
Crosby, ».«.. R.K. Tuc,er and N. Aharonson. 1966. The detection of acute
toxicity with Daphnia -asna. Food Cosmet . Toxicol. 4:503-514.
Cubing, C.E., Jr. and J.R. Olive. 1956. Effects of to.aphene and rotenone
Upo» the macroscopic bottom fauna of two northern Colorado reservoirs.
Trans. Am. Fish. Soc . 86:294-301.
Davido», .. and .... Sabatino. 1954. Biological screening test for chlorinated
U..ctUid... J. Assoc. Off. Agric. Chem. 37:902-905.
. oavis, H.C. and H. Hidu. 1969. Effect, of pesticides on embryonic development
of clam, and oysters and on survival and growth of the larvae. Fish. »uU.
67:393-404.
Davi, P «., J.M. Friedhoff and G.A. Wedemeyer. 1972. Organochlorine
in,ecticide, herbicide and polychlorinated biphenyl (PC.) inhibition of NaK-
ATPase in rainbow trout. Bull. Environ. Contam. Toxicol . 8:69-72.
Department o£ National Health and Welfare. 1977. Toxaphene. 77-EHD-ll.
Ottawa, Canada.
63
-------
Desaiah, D. and R.B. Koch. 1977. Influence of solvents on the pesticide
inhibition of ATPase activities in fish and insect tissue homogenates.
Ball. Environ. Contam. Toxicol. 17:74-78.
Dick, M. 1982. Pesticide and PCB concentrations in Texas-water, sediment,
and fish tissue. Report 264. Texas Department of Water Resources, Austin, TX.
Doudoroff, P., M. Katz and C.M. TarzweLl. 1953. Toxicity of some organic
insecticides to fish. Sewage Ind. Wastes 25:840-844.
Durant, C.J. and R.J. Reimold. 1972. Effects of estuarine dredging of
toxaphene contaminated sediments in Terry Creek. Brunswick, Ga. - 1971.
Pestic. Monit. J. 6:94-96.
Durkin, P.R., P.H. Howard, J. Saxena, S.S. Lande, J. Santodonato, J.R.
Strange and D.H. Christopher.. 1979. Reviews of the environmental, effects of
pollutants: X. Toxaphene. PB81-132409 or EPA-600/1-79-044. National Technical
Information Service, Springfield, VA.
Dziuk, L.J. and F.W. Plapp. 1973. Insecticide resistance in mosquitofish
from Texas. Bull. Environ. Contam. Toxicol. 9:15-19.
Earnest, R. 1970. Effects of pesticides on aquatic animals in the estuarine
and marine environment. In: Progress in sport fishery research, 1970. Resource
Publication 106. U.S. Bureau of Sport Fisheries and Wildlife 106, Washington,
DC. pp. 10-13.
Eckert, J.E. 1949. Determining toxicity of agricultural chemicals to honey
bees. J. Econ. Entomol. 42:261.
-------
Eisenberg, M. and J.J. Topping. 1984. Organochlorine residue in shellfish
from Maryland waters, 1976-80. J. Environ. Sci. Health 519:673-688.
Elder, J.F. and H.C. Mattraw, Jr. 1984. Accumulation of trace elements,
pesticides, and polychlorinated biphenyls in sediments and the clam Corbicula
manilensis of the Apalachicola River, Florida. Arch. Environ. Contam.
Toxicol. 13:453-469.
Epps, E.A., F.L. Bonner, L.D. Newsome, R. Carlton and R.O. Smitherman. 1967.
Preliminary report on a pesticide monitoring study in Louisiana. Bull.
Environ. Contam. Toxicol. 2:333-339.
Ferguson, D.E. 1968. Characteristics and significance of resistance to
insecticides in fishes. Reservoir Fishery Resources Symposium, Athens, GA,
. April 5-7, 1967.
Ferguson, D.E. and C.R. Bingham. 1966. The effects of combinations of
insecticides on susceptible and resistant mosquito fish. Bull. Environ.
Contam. Toxicol. 1:97-103.
Ferguson, D.E., D.D. Culley, W.D. Cotton and R.P. Dodds. 1964. Resistance
to chlorinated hydrocarbon insecticides in three species of freshwater
fish. BioScience 14:43-44.
Ferguson, D.E., D.D. Culley and W.D. Cotton. 1965a. Tolerances of two
populations of fresh water shrimp to five chlorinated hydrocarbon insecticides
J. Miss Acad. Sci. 11:235-237.
Ferguson, D.E., W.D. Cotton, D.T. Gardner and D.D. Culley. 1965b. Tolerances
to five chlorinated hydrocarbon insecticides in two species of fish from a
transect of the lower Mississippi River. J. Miss. Acad. Sci. 11:239-245.
-------
Fleming, W.J. and B.W. Cain. 1985. Areas of localized organochlorine
contamination in Arizona and New Mexico. Southwest. Nat. 30:269-277.
Frear, D.E.fl. and J.E. Boyd. 1967. Use of Daphnia magna for the microbioassay
of pesticides. I. Development of standardized techniques for rearing Daphnia
and preparation of dosage-mortality curves for pesticides. J. Bcon. Entomol.
60:1228-1236.
Gallagher, J.L., S.E. Robinson, W.J. Pfeiffer and D.M. Seliskar. 1979.
Distribution and movement of toxaphene in anaerobic saline marsh soils.
Hydrobiolgia 63:3-9.
Ginn, T.M. and F.M. Fisher, Jr. 1974. Studies on the distribution and flux
of pesticides in waterways associated with a ricefield - marshland ecosystem.
Pestic. Mont. J. 8:23-32.
Goodman, L.R. 1986. Toxaphene entire life-cycle test results for sheepshead.
minnows. U.S. EPA, Gulf Breeze, FL. (Memorandum to D.J. Hansen, U.S.
EPA, Narragansett, RI.)
Goodman, L.R., D.J. Hansen, J.A. Couch and J. Forester. 1976. Effects of
heptachlor and toxaphene on laboratory-reared embryos and fry of sheepshead
minnow. Proc. Annu. Conf. Southeast Assoc. Game Fish Comm. 30:192-202.
Grahl, K. 1983. The classification of materials contained in water according
to their toxicity potential to water organisms. Acta Hydrochim. Hydrobiol.
11:137-143.
Grzenda, A.R., G.J. Lauer and H.P. Nicholson. 1964, Water pollution by
insecticides in an agricultural river basin. II. The zooplanktcm, bottom
fauna, and fish. Limnol. Oceanogr. 9:318-323.
-------
Hall LW., Jr., t.O. Horseman and S. Zeger. 1984. Effects of organic and
inorganic che.ic.1 continent, on fertilisation, hatchin, success, and
survival of striped bass. Arch. Environ. Contam. Toxicol. 13:723-729.
Hall . J. and D. S.ineford. 1980. Toxic effects of endrin and toxaphene on the
southern Leopard frog R^ ipHenoc^la. Environ. Pollut. (Serie, A, 23:53-65.
Hall ..,. and O.M. Swineford. 1981. Acute to.icities of toxaphene and endrin
„ larvae of seven species of amphibians. Toxicol. Lett. 8:331-336.
Hannon, M.R. , .... Oreichus, l.L. APPle8ate and A.C. Pox. 19,.. Eco!ogical
distribution of pesticides in La.e Poinsett, South Da,ota. Trans. ta. Il.h.
Soc. 99:496-500.
Hansen, ».J. 1980. «... «
U.S. EPA, Duluth, MH. August 25,)
Hansen D.J. and M.E. Tagat2. 1980. A laboratory test for assessing Upacts
OE 3ubst.nces on developing communities of benthic estuarine organises. !»:
Aqu,tic toxicology. Eaton, J.O., P.I. Parrish and A.C. Hendric,, (Eds.).
,STM STP 707. American Society for Testing and Materials, Philadelphia, PA.
pp. 40-57.
Harder, ..... I.V. Carter and t.». »idle»an. 1983. Acute effect, of toxapnene
and it, sediment-degraded products on estuarine fish. Can. J. «.h. A,uat .
Sci. 40:2119-2125.
Haseltine, S.D., M.T. Pinley and .. Cro«artie. 1980. Reproduction and
residue accusation in bl«* duc.s fed toxaphene. Arch. Environ. Contam.
Toxicol. 9:461-471.
67
-------
Haseltine, S.D., O.H. Heinz, >.l. *"
-------
HiUibran, R.C. 1974. Oxygen and phosphate metabolism of bluegill live.
mitochondria in the presence »« «- i-cticides. trans. !U. State Acad.
Sci. 67:228-237.
HiUibran, R.C. 1982. Effect, of insecticides on the metal-activated
hydrolysis of adenosine trlphosphate by bluegill liver mitochondria. Arch.
Environ. Contam. toxicol. 11:709-717.
Hoiden, A.V. 1981. Or^anochiorines - an overview Mar. PoUut. BuU. 12:110-
115.
HoUstead, R.L., S. Khalifa and J.E. Casida. 1974. Toxaphen. co-position
analyzed by combined gas chromatography - chemical ioni.ation mass
5pectro»etry. J. Agric. Food Chen, 22:939-944.
Hooper, ».f. and A.R. Gr.enda. 1955. the use of to.aphene as a fish poison.
Trans. Am. Fish. Soc. 85:180-190.
Hughes R.A., G.D. Veith and G.F. Lee. 1970. Gas chromatographic analysis
Of to*aphene in natural „.«.. fish and la.e sediments. Water Res. 4:547-558.
Uensee, A.R. , a.E. ,«».. — «cCann and ,.S. Pitcher. 197,. To.icity
and fate of nine toxaphene fractions in an aquatic model ecosystem. J. Agr.c.
Food Chem. 27:1041-1046.
Johnson, D.W. and S. Lew. 1970. Chlorinated hydrocarbon pesticides in
Cepr,sentative fishes of southern Arizona. Pestic. Monit. J. 4:57-61.
.ohnson, ..... G.F. Lee and 0. SpyridaKis. 1966. Persistence of toxaphene in
treated lakes. Air Water Pollut. Int. J. 10:555-560.
69
-------
Johnson, W.W. and M.T. Finley. 1980. Handbook of acute Coxicity of chemicals
to fish and aquatic invertebrates. Resource Publication 137. U.S. Fish and
Wildlife Service, Washington, DC. pp. 77-78.
Johnson, W.W. and A.M. Julin. 1980. Acute toxicity of toxaphene to fathead
minnows, channel catfish, and bluegills. EPA-600/3-80-005. National Technical
Information Service, Springfield, VA.
Kallman, B.J., O.B. Cope and R.J. Navarre. 1962. Distribution and detoxication
of toxaphene in Clayton Lake, New Mexico. Trans. Am. Fish. Soc. 91:14-22.
Katz, M. 1961. Acute toxicity of some organic insecticides to three species
of salmonids and to the threespine stickleback. Trans. Am. Fish. Soc.
90:264-268.
Reiser, R.K., Jr., J.A. Amado and R.- Murillo. 1973. Pesticide levels in
estuarine and marine fish and invertebrates from the Guatemalan Pacific
Coast. Bull. Mar. Sci. 23:905-924.
Keith, J.O. 1966. Insecticide contaminations in wetland habitats and their
effects on fish-eating birds. J. Appl. Ecol. 3 (Suppl.):71-85.
Keith, J.O. and E.G. Hunt. 1966. Levels of insecticide residues in fish and
wildlife in California. Trans. 31st N. Am. Wildl. Nat. Resources Conf. pp.
150-177.
Khalifa, S., T.R. Mon, J.L. Engel and J.E. Casida. 1974. Isolation of 2,2,5-
endo,6-exo,8,9,10-heptachlorobornane and an octachloro toxicant from
technical toxaphene. J. Agric. Food Chera. 22:653-657.
70
-------
Khatcat, F.H. and S. Farley. 1976. Acute t«icity of c«t.U p..Ucid.. to
tonsa Dana. EPA-600/3-76-033. National Technical In£o™atlon
Springfield, VA.
K.A., D.R.
1985. Bto»n peUcan populations an, pollutant, in Texas 1975-198!. WUson
Bull. 97:201-214.
Klaas, E.E. and A.A. Belisle. 1977. Rescues in fish, wUdlife, and estua^es:
Organochlor.ne p..ticid. and polychlonnated b.phenyl residues ,n selected
Klassen, W. . W.J. Keppler and J.B. Kit»ill.r. 1965. Tox.c.ties of certain lar-
vic,des to res,stant and suscept ible ^de^ *^± U. ) - Bull. W.E.O. 33:117-122,
Korn, S. and R. Earnest. 1974. Acute toxicity of twenty insecticides to
striped bass, Morone saxatilis.. Calif. Fish Game 60:128-131.
Kuhn, A. and M. Chanunos . 1986. U.S. EPA, Narragansett , RI . (Memorandum to
D.J. Hansen, U.S. EPA, Narragansett, RI . )
Kynard, B. 1974. Avoxdance behavior of insecticides susceptible and resistant
populations of mosquitofish to four insecticides. Trans. Am. Fish. See.
103:557-561.
Lawrence, J.M. 1950. Toxicity of some new insecticides to several species
of pondfish. Prog. Fish-Cult. 12:141-146.
LeBlanc, G.A. 1984. Interspecies relationships in acute toxxcity of chemicals
to aquatic organisms. Environ. Toxicol. Chem. 3:47-60".
71
-------
Lee, G.F., R.A. Hughes and G.D. Veith. 1968. Persistence of toxaphene in
treated lakes. Progress Report to the Wisconsin Conservation Division, Oct.-
Mar. 1977-78.
Lee, G.F., R.A. Hughes and G.D Veith. 1977. Evidence for partial degradation
of toxaphene in the aquatic environment. Water Air Soil Pollut. 8:479-484.
Loeb, H.A. and W.H. Kelly. 1963. Acute oral toxicity of 1,496 chemicals
force-fed to carp. Special Scientific Report - Fisheries No. 471. U.S. Fish
and Wildlife Service, Washington DC.
Lowe, J.I. 1964. Chronic exposure of spot, Leiostomus xanthurus_, to sublethal
concentrations of toxaphene in seawater. Trans. Am. Fish. Soc. 93:396-399.
Lowe, J.I., P.O. Wilson and R.B. Davison. 1970. Laboratory bioauays. Circular
335. U.S. Fish and Wildlife Service, Gulf Breeze,'FL.
Lowe, J.I-, P.D. Wilson, A.J. Rick and A.J. Wilson, Jr. 1971. Chronic
exposure of oysters to DDT, toxaphene and parathion. Proc. Natl. Shellfish
Assoc. 61:71-79.
Macek, K.J. 1975. Acute toxicity of pesticide mixtures to bluegills. Bull.
Environ. Contain. Toxicol. 14:648-652.
Macek, K.J. and W.A. McAllister. 1970. Insecticide susceptibility of some
common fish family representatives. Trans. Am. Fish. Soc. 99:20-2.7.
Macek, K.J., C. Hutchinson and O.B. Cope. 1969. The effects of temperature
on the susceptibility of bluegills and rainbow trout to selected pesticides.
Bull. Environ. Contam. Toxicol. 4:174-183.
72
-------
Mahdi, M.A. 1966. Mortality of .o« species of fish to toxapheh, at three
temperatures. Resource Publication No. 10. U.S. Fish and Xildlif. Service,
Washington, DC.
Mahood, R.K., M.D. McKenzie, D.P. Middaugh, S.J. Bollar, J.R. Bavis and D.
Spitsbergen. 1970. A report on the cooperative blue crab study - South
Atlantic states (Project Nos . 2-79-E-l, 2-80-R-l, 2-81-R-i, and 2-82-R-l).
U.S. Department of the Interior, Bureau of Commercial Fisheries, Washington, DC.
Mayer, F.L. and P.M. Mehrle. 1978. Collagen and hydroxyproline in toxicological
studies with fishes. In: Proceedings of the first and second USA-USSR
symposia on the effects of pollutants upon aquatic ecosystems. Vol II.
Swain, W.R. and U.K. Ivanikiw (Eds.). EPA-600/3-78-076. National Technical
Information Service, Springfield, VA. pp. 92-101.
Mayer, F.L., Jr., P.M. Mehrle, Jr. and W.P. Dwyer. 1975. Toxaphene effects
on reproduction, growth, and mortality of broo. trout. EPA-600/3-75-013.
National Technical Information Service, Springfield, VA.
Mayer, F.L.. Jr., P.M. Mehrle, Jr. and W.P. Dwyer. 1977. Toxaphene: Chronic
toxiclty to fathead minnows and channel catfish. EPA-600/3-77-069. National
Technical Information Service, Springfield, VA.
Mayhew, J. 1955. Toxicity of seven different insecticides to rainbow trout
Salmo gairdnerii (Richardson). Proc. Iowa Acad. Sci. 62:599-606.
Mayhew, J. 1959. The use of toxaphene as a fish poison in strip mine ponds
with varying physical and chemical characteristics. Proc. Iowa Acad. Sci.
66:513-517.
73
-------
McDonald, S. 1962. Rapid detection of chlorinated hydrocarbon insecticides
in aqueous suspension with Gammarus Ucustris. Ucustris (Sars). Can. J.
Zool. 40:719-723.
McKenzie, M.D. 1970. Fluctuations in abundance of the blue crab and factors
affecting mortalities. Technical Report No. 1 for Project 2-79-R-l. South
Carolina Wildlife Resources, Charleston, SC.
Mehrle, P.M. and F.L. Mayer, Jr. 1975a. Toxaphene effects on growth and
bone composition of fathead minnows, Pimephales promelas. J. Fish Res.
Board Can. 32:593-598.
Mehrle, P.M. and F.L. Mayer, Jr. 1975b. Toxaphene effects on growth and
development of brook trout (Salvelinus fontinalis). J. Fish. Res,, Board
Can. 32:609-613.
Mehrle, P.M., M.T. Finley, J.L. Ludke, F.L. Mayer and T.E. Kaiser. 1979.
Bone development in black ducks as affected by dietary toxaphene. Pestic.
Biochem. Physiol. 10:168-173.
Mills, W.L. 1977. Bioassay procedure to evaluate the acute to toxicity of
salinity and geothermal pollutants (pesticides) to Gambusia affinis. UCRL-
13832. National Technical Information Service, Springfield, VA.
Moffet, G.B. and J.D. Yarbrough. 1972. The effect of DDT, toxaphene, and
dieldrin on succinic dehydrogenase activity in insecticide-resistant and
susceptible Gambusia affinis. J. Agric. Food Chem. 20:558-560.
Moore, J.C. 1981. U.S. EPA, Gulf Breeze, FL. (Memorandum to D.J. Hansen,
U.S. EPA, Gulf Breeze, FL. April 7.)
74
-------
Munson, T.O. 1976. A note oa toxapheae La environmental samples from the
Chesapeake Bay region. Bull. Environ. Contam. Toxicol. 16:491-494.
Musial, C.J. and J.F. Uthe. 1983. Widespread occurrence of the pesticide
toxaphene in Candian east coast marine fi.h. lat. J. Env.ron. Anal. Chem.
14:117-126.
Naqvi, S.M. and D.E. Ferguson. 1968. Pesticxde tolerances of selected
freshwater invertebrates. J. Miss. Acad. Sci. 14:121-127.
Naqvi, S.M. and D.E. Ferguson. 1970. Levels of insecticide resistance in
f.esh-water shrimp, P^-nonete_s k^diakensi.. Trans. Am. Fi.h. Soc. 99:696-699.
Nash, R.G. and E.A. Woolson. 1967. Persistence of chlorinated hydrocarbon
insecticides in soils. Science 157:922-927.
Needham, R.G. 1966. Effects of toxaphene on plankton and aquatic invertebrate.
Ln North Dakota lakes. Resource Publication No. 8. U.S. Fish and Wildlife
Service, Washington, DC.
Nelson, J.O. and F. Matsumura. 1975a. A simplified approach to studies of
toxic toxaphene components. Bull. Environ. Contam. Toxicol. 13:464-470.
Nelson, J.O. and F. Matsumura. 1975b. Separation and comparative toxicity
of toxaphene components. J. Agric. Food Chem. 23:984-990.
Niethammer, K.R., D.H. White, T.S. Baskett and M.W. Sayre. 1984. Presence
and biomagnification of organochlor.ne chemical residues in oxbow lakes of
northeastern Louisiana. Arch. Environ. Contam. Toxicol. 13:63-74.
75
-------
Niitni, A.J. 1985. Use of Laboratory studies in assessing the behavior of
contaminants in fish inhabiting natural ecosystems. Water Pollut. Res. Can.
20:79-88.
Nimmo, D.R. 1977. U.S. EPA, Gulf Breeze, FL. Toxaphene: Its effects on
mysids. (Memorandum to F. Hagman, U.S. EPA, Washington, DC. June.)
Nimmo, D.R., T.L. Hamaker, E. Matthews and J.C. Moore. 1981. An overview of
the acute and chronic effects of first and second generation pesticides on
an estuarine mysid. In: Biological monitoring of marine pollutants. Vernberg,
F.J., A. Calabrese, F.P. Thurberg and W.B. Vernberg (Eds.). Academic Press,
New York., NY. pp. 3-19.
Ohlendorf, H.M. and M.R. Miller. 1984. Organochlorine contaminants in
California waterfowl. J. Wildl. Manage. 48:867-877.
Ohlendorf, H.M., D.M. Swineford and L.N. Locke. 1981. Organochlorine residues
and mortality of herons. Pestic. Monit. J. 14:125-135.
Ohlendorf, H.M., J.C. Bartonek. G.J. Divoky, E.E. Klass and A.J. Krynitsky.
1982. Organochlorine residues in eggs of Alaskan seabirds. Special
Scientific Report - Wildlife No. 245. U.S. Fish and Wildlife Service,
Washington, DC.
Ohlendorf, H.M., F.C. Schaffner, T.W. Custer and C.J. Stafford. 1985.
Reproduction and Organochlorine contaminants in terns at San Diego Bay.
Colonial Waterbirds 8:42-53.
Palawski, D., J.B. Hunn and F.J. Dwyer. 1985. Sensitivity of young striped
bass to organic and inorganic contaminants in fresh and saline waters.
Trans. Am. Fish. Soc. 114:748-753.
76
-------
Paris, D.F., D.L. Lewis and J.T. Barnett. 1977. Bioconcentration of toxaphene
by microorganisms. Bull. Environ. Contam. Toxicol. 17:564-572.
Plumb, J.A. and R.W. Richburg. 1977. Pesticide levels in sera of moribund
channel catfish from a continuous winter mortality. Trans. Am. Fish. Soc.
106:185-188.
Pollock, G.A. and W.W. Kilgore. 1978. Toxaphene. Residue Rev. 69:87-140.
Rawlings, G.D. and M. Samfield. 1979. Toxicity of secondary effluents from
textile plants. EPA-600/7-78-168. National Technical Information Service,
Springfield, VA.
Reimold, R.J. 1974. Toxaphene interactions in estuarine ecosystems. Technical
Report Series No. 74-6. Georgia Marine Science Center, University System of
Georgia, Skidaway Island, GA.
Reimold, R.J. and C.J. Durant. 1974. Toxaphene content of estuarine fauna
and flora before, during, and after dredging toxaphene-contaminated sediments.
Pestic. Monit. J. 8:44-49.
Ribick, M.A., G.R. Dubay, J.D. Petty, D.L. Stalling and C.J. Schmitt. 1982.
Toxaphene residues in fish: Identification, quantification, and confirmation
at part per billion levels. Environ. Sci. Technol. 16:310-318.
Rice, C.P. and M.S. Evans. 1984. Toxaphene in the Great Lakes. In: Toxic
contaminants in the Great Lakes. Nriagu, J.O. and M.S. Simmons (Eds.). Wiley,
New York, NY. pp. 163-194.
Rice, C.P., P.J. Samson and G. Noguchi. Manuscript. Atmospheric transport
of toxaphene to Lake Michigan. U.S. EPA, Grosse lie, MI.
77
-------
Rose, E. 1958. Further notes on toxaphene in fish population control. Iowa
State Conservation Commission Quarterly Biological Report 10.
Saleh, M.A., W.V. Turner and J.E. Casida. 1977. Polychlorobornane components
of toxaphene: Structure-toxicity relations and metabolic reductive
dechlorination. Science 198:1256-1258.
Sanders, H.O. 1969. Toxicity of pesticides to the crustacean Gammarus lacustris
Technical Paper No. 25. U.S. Fish and Wildlife Service, Washington, DC.
Sanders, H.O. 1970. Pesticide toxicities to tadpoles of the western chorus
frog Pseudacris triseriata and fowler's toad Bufo woodhousii fogleri. Copeia
2:246-251.
Sanders, H.O. 1972. Toxicity of some insecticides to four species of
malacostracan crustaceans. Technical Paper No. .66. U.S. Fish and Wildlife
Service, Washington, DC.
Sanders, H.O. 1980. Sublethal effects of toxaphene on daphnids, scuds, and
midges. EPA-600/3-80-006. National Technical Information Service, Springfield,
VA.
Sanders, H.O. and O.B. Cope. 1966. Toxicities of several pesticides to two
species of cladocerans. Trans. Am. Fish. Soc. 95:165-169.
Sanders, H.O. and O.B. Cope. 1968. The relative toxicities of several
pesticides to naiads of three specices of stoneflies. Limnol. Oceanogr.
13:112-117.
Schaper, R.A. and L.A. Crowder. 1976. Uptake of 36cl.toxaphene in mosquito
fish Gambusia affinis. Bull. Environ. Contam. Toxicol. 15:581-587.
78
-------
Schimmel, S.C., J.M. Patrick, Jr. and J. Forester. 1977. Uptake and toxicity
of toxaphene in several estuarine organisms. Arch. Environ. Contam. Toxicol.
5:353-367.
Schmitt, C.J. and P.V. Winger. 1980. Factors controlling the fate of
pesticides in rural watersheds of the lower Mississippi River Alluvial
Valley. Transactions of the 45th North American Wildlife and Natural
Resources Conference. Wildlife Management Institute, Washington, DC. pp.
354-375.
Schmitt, C.J., J.L. Lajicek and M.A. Ribick. 1985. National pesticide
monitoring program: Residues of organochlorine chemicals in freshwater
fish, 1980-81. Arch. Environ. Contain. Toxicol. 14:225-260.
Schoettger, R.A. and J.R. Olive. 1961. Accumulation of toxaphene by fish-
food organisms. Limnol. Oceanogr. 6:216-219.
Seiber, J.N., S.C. Madden, M.M. McChesney and W.L. Winterlin. 1979. Toxaphene
dissipation from treated cotton field environments: Component residual
behavior on leaves and in air, soil, and sediments determined by capillary
gas chromatography. J. Agric. Food Chem. 27:284-291.
Shea, T.B. and E.S. Berry. 1982a. Uptake and toxicity of toxaphene to cell
cultures derived from goldfish (Carassius auratus). Bull. Environ. Contam.
Toxicol. 29:68-75.
Shea, T.B. and E.S. Berry. 1982b. Chronic exposure of goldfish-derived cell
cultures to toxaphene alters the replication of goldfish virus-2. Bull.
Environ. Contam. Toxicol. 19:731-733.
79
-------
Sidwell, V.D. 1981. Chemical and nutritional composition of finfishes,
whales, crustaceans, molluscs, and their products. NOAA technical memorandum
NMFS F/SEC-11. National Marine Fisheries Service, Southeast Fisheries Center,
Charleston, SC.
Smith, S. and G.H. Willis. 1978. Disappearance of residual toxaphene in a
Mississippi delta soil. Soil Sci. 126:87-93.
Stadnyk, L., R.S. Campbell and B.T. Johnson. 1971. Pesticide effect on
growth and C14 assimilation in a freshwater alga. Bull. Environ. Contam.
Toxicol. 6:1-8.
Stanley, C.W., J.E. Barney II, M.R. Helton and A.R. Yobs. 1971. Measurement
of atmospheric levels of pesticides. Environ. Sci. Technol. 5:430-435.
Stephan, C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A.
Brungs. 1985. Guidelines for deriving numerical national water quality
criteria for the protection of aquatic organisms and their uses. PB85-
227049. National Technical Information Service, Springfield, VA.
Stringer, G.E. and R.G. McMynn. 1958. Experiments with toxaphene as a fish
poison. Can. Fish. Cult 23:1-8.
Stringer, G.E. and R.G. McMynn. 1960. Three years' use of toxaphene as a
fish toxicant in British Columbia. Can. Fish. Cult. 28:37-44.
Surber, E.W. 1948. Chemical control agents and their effects on fish. Prog.
Fish.-Cult. 10:125-131.
-------
suain ..».. M... Mullin and J.C. FiUU.. »«• -g range transport
0£ toxic organic contaminants to the -th American -at — *"
o£
o£
R.C. (Ed.). EPA-600/9-86-004. Nation.! Technical Infor.ation S.rv.ce,
Springfield, VA
S.a.0 R.C., ..C. Coon and .. Koi.e. 197,. P...I.U. and ?CB of co«on
'
Toxicol. 22:394-399.
. L.C.. and
animals. J/Agric. Food Che». 14:66-69.
Turner «.».. 8. Knalifa an. J.». Casida. 1975. To.apnene toxicanc A.
Mi^ure of 2,2,5-endo,6-exo,8,8,9,10-ocCachloCobornane and 2,2,5-endo,6-
eXo,8,9,9,10-ocCachlorobornane. J. Agri=. Food Chem. 23:991-994.
Turner, W.V., J.L. Engel and J.E. Casida. 1977. To.aphene component and
r.l«- compound,: Preparation and t«Ul.T •' «- •»»"-' °«- "d
nonachlorobornane8, -a- and heptachlorobornene, , and a he,achlorobornadiene
J. Agric. Food Chem. 25:1394-1401.
m»l... - 196». Gro«K of pure cuitures of .arine p.ytoplan.ton in the
presence of toxicant,. Appl. Environ. Microbiol. 10:532-537.
U.S. Bureau of Commercial Fisheries. 1965. Unpublished laboratory data.
Environmental Research Laboratory, Gulf Bree.e, FL.
81
-------
U.S. Bureau of Commercial Fisheries. 1967. Unpublished laboratory data.
Environmental Research Laboratory, Gulf Breeze, PL.
U.S. EPA. 1976. Quality criteria for water. EPA-440/9-76-023. National
Technical Information Service, Springfield, VA.
U.S. EPA. 1980. Ambient water quality criteria for toxaphene. EPA-440/5-80-076.
National Technical Information Service, Springfield, VA.
U.S. EPA. 1983a. Water quality standards regulation. Fed. Regist. 48:51400-
51413. November 8.
U.S. EPA. 1983b. Water quality standards handbook. Office of Water Regulations
and Standards, Washington, DC.
U.S. EPA. 1985a. Appendix B - Response to public comments on "Guidelines for
deriving numerical national water quality criteria for-the protection of
aquatic organisms and their uses." Fed. Regist. 50:30793-30796. July 19.
U.S. EPA. 1985b. Technical support document for water-quality based toxics
control. Office of Water, Washington, DC. September.
U.S. EPA. 1986. Chapter 1 - Stream design flow for steady-state modeling. In:
Book VI - Design conditions. In: Technical guidance manual for performing
waste load allocations. Office of Water, Washington, DC.
U.S. Food and Drug Administration. 1985. Action levels for poisonous or
deleterious substances in human food and animal food. Center for Food Safety
and Applied Nutrition, Industry Programs Branch, Washington, DC. p. 13.
Veith, G.D. and G.F. Lee. 1971. Water chemistry of toxaphene - role of lake
sediments. Environ. Sci. Technol. 5:230-234.
82
-------
von Ru^er, ... E.W. L«l.... A.F. M.iners , l.A. Lawrence, G.L. Kelso and
F Koray. 1974. Production, distribution, use and environmental impact
potential of selected pesticides. EPA- 540 A -74-001 or PB-238795. National
Technical Information Service, Springfield, VA. pp. 196-204.
Walsh, G.E., K.M. Dufce and R.B. Foster. 1982. Algae and crustaceans as
indicators of bioactivity of industrial wastes. «.ter Res. 16:879-883.
Warner, I.E., «. Person «* >•• •«•— ' 1966'
fish: A quantitative study of sublethal pesticide toxication. J. Appl.
Ecol. 3:223-247.
Webb, D.W. 1980. The effects of toxaphene piscicide on benthic macro-
invertebrates. J. Kans. Entotnol. Soc. 53:731-744.
Weber, F.H. and F.A. Rosenberg. 1980. Biological stability of toxaphene in
estuarine sediment. Bull. Environ. Contatn. Toxicol. 25:85-89.
Weber, F.H., T.B. Shea and E.S. Berry. 1982. Toxicity of certain insecticides
to protozoa. Bull. Environ. Contam. Toxicol. 28:628-631.
Whitacre, D.M., C.C. Roan and G.W. Ware. 1972. Pesticides and aquatic
microorganisms. Search 3:150-157.
White, D.H., R.C. Stendell and B.M. Mulhern. 1979. Relations of wintering
canvasbacVes to environmental pollutants - Chesapeake Bay, Maryland. Wilson
Bull. 91:279-287.
White, D.H., K.A. King and R.M. Prouty. 1980. Significance of organochlorine
and heavy metal residues in wintering shorebirds at Corpus Christi, Texas,
1976-77. Pestic. Monit. J. 14:58-63.
83
-------
White, D.H., C.A. Mitchell and R.M. Prouty. 1983. Nesting biology of laughing
gulls in relation to agricultural chemicals in south Texas, 1978-81. Wilson
Bull. 95-540-551.
Wideqvist, U., B. Jansson, L. Reutergardh and G. Sundstrom. 1984. The
evaluation of an analytical method for polychlorinated terpenes (PCC) in
biological samples using an internal standard. Chemosphere 13:367-379.
Wiemeyer, S.N., T.G. Lamont, C.M. Bunck, C.R. Sindelar, F.J. Gramlich, J.D.
Fraser and M.A. Byrd. 1984. Organochlorine pesticide, polychlorobiphenyl, and
mercury residues in bald eagle eggs - 1969-79 - and their relationships to
shell thinning and reproduction. Arch. Environ. Contam. Toxicol. 13:529-549.
Winger, P.V., C. Sieckman, T.W. May and W.W. Johnson. 1984. Residues of organo-
chlorine insecticides, polychlorinated biphenyls, and heavy metals in biota
from Apalachicola River, Florida, 1978. J. Assoc. Off. Anal. Chem. 67:325-333.
Wollitz, R.E. 1962. Effects of certain commerical fish toxicants on the
limnology of three cold-water ponds, Montana. Proc. Mont. Acad. Sci. 22:54-81.
Workman, G.W. and J.M. Neuhold. 1963. Lethal concentrations of toxaphene
for goldfish, mosquitofish, and rainbow trout, with notes on detoxification.
Prog. Fish-Cult. 25:23-30.
Yarbrough, J.D. and J.E. Chambers. 1979. The disposition and biotransformation
of organochlorine insecticides in insecticide-resistant and -susceptible
mosquitofish. In: Pesticide and xenobiotic metabolism in aquatic organisms.
Khan, M.A.Q., J.J. Lech and J.J. Menn (Eds.). ACS Symposium Series No. 99.
American Chemical Society, Washington, DC.
84
-------
Zaroogian, G.E., J.F. HeHshe and M. **„«. 1985. Estimation o£ ^concentration
in marine specie, U,ing .tra«««cti«t, -d.1- -iron. To.icol. One.. *:3-».
zell, M. and K. Ballschuiter. 1980. Baseline 3tudie, o£ the global pollution.
„ Globa! occurrence of hexachlorobenzene (HOB) and polychlotocaaphene,
(ToxapKene.) (POC) in biologica! sa.ple3. Freseniu, Z. Anal. Cbe«. 300:387-402.
Zygad!o, L.V. 1982. Oo»estic usage of toxaphene. U.S. EPA, Office of
Pesticide Programs, Economic Analysis Branch, Washington, DC.
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