United Slates Office of Water EPA 440/5-80-027
Environmental Protection Regulations and Standards October 1980
Agency Criteria and Standards Division
Washington DC 20460 £,
v>EPA Ambient
Water Quality
Criteria for
Chlordane
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AMBIENT WATER QUALITY CRITERIA FOR
CHLORDANE
Prepared By
U.S. ENVIRONMENTAL PROTECTION AGENCY
Office of Water Regulations and Standards
Criteria and Standards Division
Washington, D.C.
Office of Research and Development
Environmental Criteria and Assessment Office
Cincinnati, Ohio
Carcinogen Assessment Group
Washington, D.C.
Environmental Research Laboratories
Corvalis, Oregon
Duluth, Minnesota
Gulf Breeze, Florida
Narragansett, Rhode Island
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DISCLAIMER
This report has been reviewed by the Environmental Criteria and
Assessment Office, U.S. Environmental Protection Agency, and approved
for publication. Mention of trade names or commercial products does not
constitute endorsement or recommendation for use.
AVAILABILITY NOTICE
This document is available to the public through the National
Technical Information Service, (NTIS), Springfield, Virginia 22161.
11
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FOREWORD
Section 304 (a)(l) of the Clean Water Act of 1977 (P.L. 95-217),
requires the Administrator of the Environmental Protection Agency to
publish criteria for water quality accurately reflecting the latest
scientific knowledge on the kind and extent of all identifiable effects
on health and welfare which may be expected from the presence of
pollutants in any body of water, including ground water. Proposed water
quality criteria for the 65 toxic pollutants listed under section 307
(a)(l) of the Clean Water Act were developed and a notice of their
availability was published for public comment on March 15, 1979 (44 FR
15926), July 25, 1979 (44 FR 43660), and October 1, 1979 (44 FR 56628).
This document is a revision of those proposed criteria based upon a
consideration of comments received from other Federal Agencies, State
agencies, special interest groups, and individual scientists. The
criteria contained in this document replace any previously published EPA
criteria for the 65 pollutants. This criterion document is also
published in satisifaction of paragraph 11 of the Settlement Agreement
in Natural Resources Defense Council, et. al. vs. Train, 8 ERC 2120
(O.D.C. 1976), modified, 12 ERC 1833 (D.D.C. 1979).
The term "water quality criteria" is used in two sections of the
Clean Water Act, section 304 (a)(l) and section 303 (c)(2). The term has
a different program impact in each section. In section 304, the term
represents a non-regulatory, scientific assessment of ecological ef-
fects. The criteria presented in this publication are such scientific
assessments. Such water quality criteria associated with specific
stream uses when adopted as State water quality standards under section
303 become enforceable maximum acceptable levels of a pollutant in
ambient waters. The water quality criteria adopted in the State water
quality standards could have the same numerical limits as the criteria
developed under section 304. However, in many situations States may want
to adjust water quality criteria developed under section 304 to reflect
local environmental conditions and human exposure patterns before
incorporation into water quality standards. It is not until their
adoption as part of the State water quality standards that the criteria
become regulatory.
Guidelines to assist the States in the modification of criteria
presented in this document, in the development of water quality
standards, and in other water-related programs of this Agency, are being
developed by EPA.
STEVEN SCHATZOW
Deputy Assistant Administrator
Office of Water Regulations and Standards
111
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ACKNOWLEDGEMENTS
Aquatic Life Toxicology:
William A. Brungs , ERL-Narragansettt D. J. Hansen, ERL-Duluth
U.S. Environmental Protection Agency U.S. Environmental Protection Agency
Mammalian Toxicology and Human Health Effects:
Herbert R. Pahren, HERL (author) John Doull
U.S. Environmental Protection Agency University of Kansas Medical Center
Terence M. Grady (doc. mgr.) Kris Khanna, ODW
ECAO-Cin U.S. Environmental Protection Agency
U.S. Environmental Protection Agency
Fumio Matsamura Shane Que Hee
Michigan State University University of Cincinnati
Joseph Santodonato Anne Trontell
Syracuse Research Corporation Energy Resources Co.
Roy E. Albert *
Carcinogen Assessment Group
U.S. Environmental Protection Agency
Technical Support Services Staff: D.J. Reisman, M.A. Garlough, B.L. Zwayer,
P.A. Daunt, K.S. Edwards, T.A. Scandura, A.T. Pressley, C.A. Cooper,
M.M. Denessen.
Clerical Staff: C.A. Haynes, S.J. Faehr, L.A. Wade, D. Jones, B.J. Bordicks,
B.J. Quesnell, C. Russom, R. Rubinstein.
*CAG Participating Members: Elizabeth L. Anderson, Larry Anderson, Dolph Arnicar,
Steven Bayard, David L. Bayliss, Chao W. Chen, John R. Fowle III, Bernard
Haberman, Charalingayya Hiremath, Robert McGaughy, Jeffrey Rosenblatt, Chang S. Lao
Dharm V. Singh, and Todd W. Thorslund.
IV
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TABLE OF CONTENTS
Page
Criteria Summary
Introduction A-l
Aquatic Life Toxicology B-l
Introduction B-l
Effects B-l
Acute Toxicity B-l
Chronic Toxicity B-3
Plant Effects B-4
Miscellaneous B-6
Summary B-6
Criteria B-7
References B-22
Mammalian Toxicology and Human Health Effects C-l
Exposure C-l
Ingestion from Water C-l
Ingestion from Food C-2 '
Inhalation C-4
Dermal C-4
Pharmacokinetics C-5
Absorption C-5
Distribution C-5
Metabolism C-6
Excretion C-7
Effects C-8
Acute, Subacute, and Chronic Toxicity C-8
Synergism and Antagonism C-ll
Teratogenicity C-l 2
Mutagenicity C-l 2
Carcinogenicity C-12
Criterion Formulation C-18
Existing Guidelines and Standards C-18
Current Levels of Exposure and Special
Groups at Risk C-18
Basis and Derivation of Criterion C-19
References C-23
Appendix C-31
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CRITERIA DOCUMENT
CHLORDANE
CRITERIA
Aquatic Life
For chlordane the criterion to protect freshwater aquatic life as de-
rived using the Guidelines is 0.0043 yg/1 as a 24-hour average, and the con-
centration should not exceed 2.4 pg/1 at any time.
For chlordane the criterion to protect saltwater aquatic life as derived
using the Guidelines is 0.0040 ug/1 as a 24-hour average, and the concentra-
tion should not exceed 0.09 pg/1 at any time.
Human Health
For the maximum protection of human health from the potential carcino-
genic effects due to exposure to chlordane through ingestion of contaminated
water and contaminated aquatic organisms, the ambient water concentration
should be zero based on the nonthreshold assumption for this chemical. How-
ever, zero level may not be attainable at the present time. Therefore, the
levels which may result in incremental increase of cancer risk over the
lifetime are estimated at 10~5, 10~6, and 10~7. The corresponding
recommended criteria are 4.6 ng/1, 0.46 ng/1, and 0.046 ng/1, respectively.
If the above estimates are made for consumption of aquatic organisms only,
excluding consumption of water, the levels are 4.8 ng/1, 0.48 ng/1, and
0.048 ng/1, respectively.
VI
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INTRODUCTION
Chlordane is a broad spectrum insecticide of the group of polycyclic
chlorinated hydrocarbons called cyclodiene insecticides. Chlordane has been
used extensively over the past 30 years for termite control, as an insecti-
cide for homes and gardens, and as a control for soil insects during the
production of crops such as corn. Production of Chlordane in the United
States approached 10,000 metric tons per year in 1974 (41 FR 7558). Both
the uses and the production volume of Chlordane have decreased extensively
since the issuance of a registration suspension notice for all food crops
and home and garden uses of chlordane by the U.S. EPA (40 FR 34456). How-
ever, significant commercial use of chlordane for termite control continues.
In addition, under the terms of a recent settlement which terminated chlor-
dane registration cancellation proceedings, chlordane will be permitted for
limited usage through 1980 as an agricultural insecticide (43 FR 12372).
Pure chlordane is a pale yellow liquid having the molecular formula
C10H6C18 and a molecu1ar weight of 409.8 (Windholz, 1976; Whetstone,
1972). The chemical name for chlordane is l,2,4,5,6,7,8,8-octachloro-2,3,-
3a,4,7,7a-hexahydro-4,7-methanoindene (Windholz, 1976). Pure chlordane is
composed of a mixture of stereoisomers, with the cis and trans forms pre-
dominating and referred to as alpha and gamma isomers, respectively (Brooks,
1974). Brooks (1974) reported the solubility of chlordane in water to be
approximately 9 ug/1 at 25°C.
Chlordane is produced by the chlorination of chlordene which, in turn,
is a product of hexachlorocyclopentadiene and cyclopentadiene (Whetstone,
1972).
A-l
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Technical grade chlordane is a mixture of various chlorinated hydrocar-
bons with a typical composition of approximately 24 percent trans(gamma)-
chlordane, 19 percent (iis(alpha)chlordane, 10 percent heptachlor, 21.5 per-
cent chlordene isomers, 7 percent nonachlor, and 18.5 percent closely relat-
ed chlorinated hydrocarbon compounds (Velsicol Chemical Corp., 1971). Tech-
nical chlordane is a viscous, amber-colored liquid with a cedar-like odor
and is relatively nonvolatile, having a vapor pressure of 1 x 1CT5 mm Hg
at 25°C; it is soluble in water (150 to 220 wg/l at 22°C) and has a density
greater than that of water, approximately 1.65 g/ml at 16°C (Metcalf, 1955;
Whetstone, 1972; Cardwell, et al. 1977).
Chlordane has been detected at various concentrations in ambient water,
finished drinking water, rainwater, and soils. Chlordane is readily soluble
in natural fats and fat soluble substances (Brooks, 1974). Chlorane has
been found in plankton, earthworms, shellfish, fish, birds, bird eggs, man,
and several other mammals.
A-2
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REFERENCES
Brooks, G.T. 1974. Chforinated Insecticides. CRC Press, Cleveland, Ohio.
Cardwell, R.D., et al. 1977. Acute and chronic toxicity of chlordane to
fish and invertebrates. EPA 600/3-77-019. U.S. Environ. Prot. Agency.
Metcalf, R.L. 1955. Organic Insecticides. Interscience Publishers, Inc.,
New York.
Velsicol Chemical Corp. 1971. Standard for technical chlordane. Chicago.
Whetstone, R.R. 1972. Kirk-Othmer Encyclopedia of Chemical Technology.
John Wiley and Sons, Inc., New York.
Windholz, M. (ed.) 1976. The Merck Index. Merck and Co., Inc., Rahway,
New Jersey.
A-3
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Aquatic Life Toxicology*
INTRODUCTION
Although chlordane -4ias been used as an insecticide for many years, our
knowledge of its toxicity to aquatic life is less complete than for other
chlorinated hydrocarbon insecticides such as DDT and dieldrin. Early fresh-
water studies (Henderson, et al. 1959; Katz, 1961) using static test proce-
dures showed it to be substantially less toxic than endrin, dieldrin, DDT,
and toxaphene. Perhaps as a result, few additional data appeared in the
literature until the 1970's. Chronic data were published recently, but
dealt with only a few species. Data for bioconcentration likewise is mostly
of recent origin. The effect on aquatic plants is not well documented.
The chlordane data base for saltwater organisms is less than for fresh-
water organisms. The data are insufficient to determine the importance of
salinity, 'temperature, or other water quality factors to the toxicity of
this insecticide.
The toxicities of major chemicals in technical chlordane have not been
studied, and relative toxicity of each chemical responsible for the effects
of chlordane has not been identified.
EFFECTS
Acute Toxicity
Data from 25 tests on five freshwater invertebrate and nine fish species
met Guideline requirements for inclusion in Table 1; these data are inade-
quate to show a general difference in susceptibility between freshwater fish
*The reader is referred to the Guidelines for Deriving Water Quality
Criteria for the Protection of Aquatic Life and Its Uses in order to
understand this section better. The attached tables contain pertinent
available data, and at the bottoms of the appropriate tables are
calculations deriving vari- ous measures of toxicity as described in the
Guidelines.
B-l
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and invertebrate species. The susceptibility ranking in Table 3 appears to
show the invertebrate species to be more sensitive, but the ranked location
of the carp and Daphnia. magnaj and the variation among tests on the same spe-
cies (Table 1) offset any attempt to rank susceptibility by large taxonomic
groups. The 1C values of the tested aquatic animals range from 3 pg/1
for carp to 190 yg/1 for guppy; however, most species mean acute values lie
between 15 and 60 ug/l (Table 3). The Freshwater Final Acute Value for
chlordane, derived from the species mean acute values listed in Table 3
using the calculation procedure described in the Guidelines, is 2.4 ug/l.
Acute values for saltwater invertebrate species range from 0.4 to 480
ug/l (Tables 1 and 5). Blue crab, in a 48-hour test (Table 5), were over
1,000 times more tolerant than pink shrimp in a 96-hour test (Table 1).
Adult Oungeness crabs were also tolerant of acute chlordane exposure, with
an LCcQ value of 220 ug/l (Caldwell, 1977), but Oungeness crab zoeae had a
much lower LC5Q of 1.3 ug/l (Table 1).
Five species of saltwater fishes have been tested for the acute effects
of chlordane (Tables 1 and 5). In flow-through exposures, the 96-hour
LC[. values for three species range from 6.4 to 24.5 ug/l (Korn and Ear-
nest, 1974; Parrish, et al. 1976, 1978). Two LC5Q values for threespine
stickleback from static tests with unmeasured concentrations were 90 and 160
ug/l. The LC™ values for fish species differed by a factor of more than
25.
The minimum data base requirements for deriving a Saltwater Final Acute
Value have not been met (96-hour IC™ values are available for four in-
stead of the required five invertebrate families); however, data are
available for eight species (four invertebrate and four fish species).
Moreover, it is unlikely that the Saltwater Final Chronic Value (see Chronic
3-2
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Toxicity section) would be significantly influenced by one more acute value
for an invertebrate species. Accordingly, a Saltwater Final Acute Value for
chlordane of 0.09 ug/1 was derived from the species mean acute values listed
in Table 3 using the procedure described in the Guidelines.
Chronic Toxicity
Freshwater chronic tests have been conducted by Cardwell, et al. (1977)
on Daphnia magna and bluegill, providing chronic values for these species of
16 and 1.6 ug/l, respectively; acute-chronic ratios for these two species
are 3.6 and 37, respectively (Table 2). The only other freshwater chronic
tests reported were also conducted by Cardwell, et al. (1977) on fathead
minnow, brook trout, Hyallela azteca, and Chironomus No. 51 (Table 5). The
fathead minnow test produced no statistically significant difference at the
highest concentration tested (6.03 ug/1). Reduced embryo viability was ob-
served in brook trout during a 13-month exposure to 0.32 ug/l. Effects on
the invertebrate species occurred at concentrations as low as 1.7 ug/1; this
concentration caused mortality of chironomid larvae in a 25-day exposure
(Table 5).
No reports of life-cycle chronic tests with any saltwater invertebrate
species were found. In extended exposures of Dungeness crab zoeae and
adults to chlordane (Caldwell, 1977), 0.15 ug/1 affected moulting and was
lethal to 50 percent after 37 days of exposure. Survival and moulting were
unaffected in chlordane concentrations of 0.015 ug/1. Most adult crabs died
after a 90-day continuous exposure to 10 ug/1, but survival in 1 ug/1 did
not differ from controls (Table 5).
Chlordane was chronically toxic to the saltwater sheepshead minnow
(Table 2) in a full life-cycle- exposure at concentrations ^0.8 ug/1 (Par-
rish, et al. 1978). Survival of juveniles was reduced at 18 ug/1, and their
B-3
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survival through adulthood was reduced at 2.8 ug/l (Parrish, et al. 1978).
Reproduction of exposed adults was not impaired, but hatching of embryos was
decreased at 0.8 ug/1, and juvenile survival decreased at 1.7 wg/l. NO sig-
nificant effects were observed on survival, growth, or reproduction at a
chlordane concentration of 0.5 pg/l. The concentration not affecting sheep-
shead minnows in this chronic exposure was 0.04 of the 96-hour LC . jn
ou
an early-life-stage test on the same species, 17 pg/l was lethal to fry, but
7.1 yg/1 was not (Parrish, et al. 1976). Usually, results of early-life-
stage toxicity tests can be used to predict results of life-cycle tests.
Chlordane, because of its effects on adult fish and their progeny, is an ex-
ception to this general relationship. Therefore, the results of the life-
cycle test, rather than those of the early-life-stage test, should ue used
as a measure of chlordane's chronic toxicity to this saltwater fish species.
The Final Acute-Chronic Ratio for chlordane of 14 is the geometric mean
of the three acute-chronic ratios (Tables 2 and 3). The Freshwater Final
Acute Value of 2.4 ug/l divided by the Final Acute-Chronic Ratio of 14 re-
sults in the Freshwater Final Chronic Value for chlordane of 0.17 ug/l. The
Saltwater Final Acute Value of 0.09 wg/i divided by the Final Acute-Chronic
Ratio of 14 results in the Saltwater Final Chronic Value for chlordane of
0.0064 ug/l.
Plant Effects
Glooschenko and Lott (1977) found that 0.1 yg/l stimulated growth of a
freshwater algal species (Table 5). No data are available showing other ef-
fects on freshwater plant species. Information on the sensitivity of salt-
water aquatic plants, including algae and rooted vascular plants, is limited
to one test using a 4-hour exposure of a mixed phytoplankton community
(Table 5).
B-4
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Residues
Table 4 contains bioconcentration data for a freshwater fish and an in-
vertebrate species. For Hyaljela azteca, Cardwell, et al. (1977) reported
factors for each of seven major constituents of technical chlordane; the bi-
oconcentration factor (BCF) of 5,200 for technical chlordane shown in
Table 4 was obtained by multiplying the arithmetic mean of each constitu-
ent's BCF value by its percentage composition in technical chlordane, then
adding the products of each constituent. A BCF of 3,800 for Daphnia magna
(Cardwell, et al. 1977), shown in Table 5, was calculated in the same manner
as the Hyallela azteca factor, but the datum was not included in Table 4 be-
cause of the short duration (7 days) of the exposure.
Whole-body BCF values for the saltwater fish species, sheepshead minnow,
ranged from 6,600 to 16,000 (Table 4). Bioconcentration factors in juvenile
fish ranged from 8,500 to 12,300 after 28 days of exposure to technical
chlordane (Parrish, et al. 1976). Adult fish exposed to technical chlordane
for 189 days had BCF values ranging from 13,000 to 22,000, and a 28-day-old
progeny from the same experiment contained 6,500 to 22,000 times as much
chlordane as was measured in the test solution (Parrish, et al. 1978).
Sheepshead minnows exposed to technical heptachlor, which contains trans -
chlordane, accumulated the trans-chlordane 2,000 to 11,700 times the concen-
tration in water (Goodman, et al. 1978).
Dividing a BCF value by the percent lipid value for the same species
provides a BCF value adjusted to 1 percent lipid content; this resultant BCF
value is referred to as the normalized BCF. Percent lipid values are avail-
able for fathead minnows (Veith, 1980) and adult sheepshead minnows (Hansen,
1980). Dividing the percent lipid value of 7.6 for fathead minnows into the
BCF of 37,800 gives a normalized BCF of 4,974. Dividing the percent lipid
B-5
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value at 3.6 for sheepshead minnows into the BCF of 16,000 gives a normal-
ized BCF of 4,444. The geometric mean of these normalized BCF values is
4,702 (Table 4).
To protect the marketability of edible fish, the concentration of chlor-
dane in edible tissue cannot exceed the action level of 0.3 mg/kg estab-
lished by the U.S. Food and Drug Administration (FDA) for chlordane. The
Freshwater Final Residue Value is derived by dividing the FDA action level
of 0.3 mg/kg by the geometric mean of the normalized BCF values (4,702) and
by a percent lipid value of 15 for freshwater species (see Guidelines). The
Freshwater Final Residue Value thus obtained is 0.0043 yg/1 (Table 4). The
Saltwater Final Residue Value (Table 4) is 0.0040 yg/1, obtained by dividing
the FDA action level (0.3 mg/kg) by the geometric mean of normalized BCF
values (4,702) and by a percent lipid value of 16 for saltwater species (see
Guidelines). The Final Residue Value may be too high because, on the aver-
age, the concentration in 50 percent of species similar to those need to de-
rive the values will exceed the FDA action level.
Miscellaneous
No other data from Table 5 suggest any more sensitive effects or greater
accumulation of chlordane than those already discussed.
Summary
Acute toxicity of chlordane to freshwater fish and invertebrate species
occurs at concentrations ranging from 3 to 190 yg/1, with most values fall-
ing between 15 and 60 yg/1. Freshwater chronic values are available for one
fish (1.6 yg/1) and one invertebrate (16 yg/1) species. Bioconcentration
factors of 37,800 and 5,200 are available for one freshwater fish and one
invertebrate species, respectively. No appropriate data are available for
chlordane and any freshwater plant species. The Freshwater Final Acute Val-
B-6
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ue is 2.4 yg/1, the Freshwater Final Chronic Value is 0.17 wg/1, and the
Freshwater Final Residue Value is 0.0043 yg/1 based on the FDA action level
for edible fish.
Acute toxicity of chlordane to saltwater fish and invertebrate species
occurs at concentrations ranging from 0.4 to 480 pg/1, with the pink shrimp
being the most sensitive species. A life-cycle chronic test on the sheep-
shead minnow provided a chronic value for this species of 0.63 ug/1. No
chronic data are available for chlordane and any saltwater invertebrate spe-
cies, and no appropriate data are available for any saltwater plant species.
Bioconcentration factors for chlordane in the sheepshead minnow ranged from
6,600 to 16,000. The data base for acute toxicity of chlordane to saltwater
species lacks one invertebrate family to fulfill the minimum data base re-
quirements according to the Guidelines. However, because acute data are a-
vailable for eight species and because it is unlikely that the Saltwater
Final Chronic Value would be significantly influenced by one more acute val-
ue for an invertebrae species, a Saltwater Final Acute Value was derived for
chlordane and was calculated to be 0.09 wg/l. The Saltwater Final Chronic
Value is 0.0064 ug/1, and the Saltwater Final Residue value is 0.0040 ug/1
based on the FDA action level for edible fish.
It should be noted that the Final Residue Values may be too high be-
cause, on the average the concentration in 50 percent of species similar to
those used to derive the values will exceed the FDA action level.
CRITERIA
For chlordane the criterion to protect freshwater aquatic life as de-
rived using the Guidelines is 0.0043 pg/1 as a 24-hour average, and the con-
centration should not exceed 2.4-yg/l at any time.
B-7
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For chlordane the criterion to protect saltwater aquatic life as derived
using the Guidelines is 0.0040 wg/l as a 24-hour average, and the concentra-
tion should not exceed 0.09 ug/1 at any time.
B-8
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Table I. Acute values for cM or done
Species
Method*
Chemical**
LC50/EC50
Cua/U
Species Mean
Acute Value
(uo/l)
Reference
FRESHWATER SPECIES
Cladoceran,
Daphnla tnagna
Cladoceran,
Daphnla magna
Scud,
Gammarus fasclatus
Scud,
Gammarus lacustrls
Freshwater shrimp.
Pa 1 aemonetes kadlakensls
Freshwater shrimp,
Pa 1 aemonetes kadlakensls
CD
1 Stonefly,
Pteronarcys callfornica
Coho salmon (age 0),
Oncorhynchus klsutch
Chinook salmon (age 0),
Oncorhynchus tshawytscha
Rainbow trout (age 0),
Sal mo gair drier 1
Rainbow trout.
Sal mo galrdnerl
Rainbow trout,
Salmo galrdnerl
Brook trout (adult),
Salvel Inus fontlnal Is
Goldfish,
Carasslus auratus
S, M
S, U
S, U
S, U
S, U
FT, U
S, U
S, U
S, U
S, U
S, U
S, U
FT, M
S, U
Technical
chlordane
Techn I ca 1
ch lordane
Technical
ch lordane
Techn 1 ca 1
ch lordane
Technical
ch lordane
Technical
ch lordane
Techn 1 ca 1
ch lordane
Ch lordane
100* A.I.
Chlordane
100? A.I.
Ch lordane
1001 A.I.
Techn I ca 1
chlordane
Technical
ch lordane
Technical
ch lordane
Ch lordane
100* A.I.
35
97
40
26
10
4
15
56
57
44
47
8
45
82
58
40
26
6.3
15
56
57
25
45
82
U.S. EPA, 1980
Randall, et al. 1979
Sanders, 1972
Sanders, 1969
Sanders, 1972
Sanders, 1972
Sanders & Cope, 1968
Katz, 1961
Katz, 1961
Katz, 1961
Mehrle, et al. 1974
Mehrle, et al. 1974
Cardwel 1, et al. 1977
Henderson, et al.
1QSQ
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Table t. (Continued)
Species Method*
Carp, s, U
Cyprlnus carplo
Fathead minnow, S, U
Plmephales promelas
Fathead minnow, S, U
Plmephales promelas
Fathead minnow (juvenile), FT, M
Plmephales promelas
Guppy, S, U
Poecilla retlculata
Blueglll, s, U
Lepomls macrochlrus
w Blueglll, s, U
1 Lepomls macrochlrus
0 Blueglll, S, U
Lepomls macroch 1 rus
Bluegl II, s, U
Lepomls macrochlrus
Blueglll, FT, M
j-epomls macrochlrus
Bluegl II, s, U
Lepomls macrochlrus
Eastern oyster, FT, U
Crassostrea virglnica
Eastern oyster, FT, U
Crassostrea virglnica
Chemical**
Ch lordane
75* E.C.
Ch lordane
100* A. I .
Ch lordane
100* A. 1 .
Techn 1 ca 1
ch lordane
Ch lordane
100* A. I .
Ch tordane
100* A.I.
Technical
ch lordane
Techn 1 ca 1
ch fordane
Techn 1 ca 1
ch lordane
Techn 1 ca 1
ch lordane
Technical
ch lordane
SALTWATER
_
LC50/EC50
(Pfl/l)
3
52
69
37
190
22
77
77
85
59
41
SPECIES
7
10
Species Mean
Acute Value
(ug/D Reference
3 Rao, et al. 1975
Henderson, et al.
1959
Henderson, et al.
1959
37 Cardwell, et al. 1977
190 Henderson, et al,
1959
Henderson, et al.
1959
Macek, et al. 1969
Macek, et al. 1969
Macek, et al. 1969
Cardwell, et al. 1977
59 Randal 1, et al. 1979
Butler, 1963
Butler, 1963
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Table 1. (Continued)
w
1
1 — 1
h-1
Species
Eastern oyster,
Crassostrea virgin! ca
Pink shrimp.
Penaeus duorarum
Grass shrimp,
Pa 1 aemonetes puglo
Dungeness crab (zoeae),
Cancer maglster
Dungeness crab (adult).
Cancer maglster
Sheepshead minnow.
Cyprlnodon varlegatus
Sheepshead minnow.
Cyprlnodon varlegatus
Threesplne stickleback
(adult).
Gasterosteus aculeatus
Threesplne stickleback
(adult),
Gasterosteus aculeatus
Striped bass,
Morone saxatl 1 Is
Pinflsh,
Lagodon rhomboldes
Method* Chemical**
FT,
FT,
FT,
s,
s,
FT,
FT.
s.
s.
FT,
FT,
M
M
M
U
U
M
M
U
U
U
M
LC50/EC50
(wg/D
6.2
0.4
4.8
1.3
220
24.5
12.5
90
160
11. 6
6.4
Species Mean
Acute Value
( ug/ 1 ) Ref erence
6.2 Parrlsh, et al.
0.4 Parrlsh, et al.
4.8 Parrlsh, et al.
Caldwell, 1977
16.9 Caldwell, 1977
Parrlsh, et al.
17.5 Parrlsh, et al.
Katz, 1961
120 Katz, 1961
11.8 Korn 4 Earnest,
6.4 Parrlsh, et al.
1976
1976
1976
1976
1978
1974
1976
* S = static, FT = flow-through, U = unmeasured, M = measured
**A.I. = active Ingredient, E.C. = effective concentration
-------
Species
Table 2. Chronic values for chIordone
Test* Chemical
Limits Chronic Value
(f9/D (ug/l) Reference
Cladoceran, LC
Daphnla magna
Blueglll, LC
Lepomls macrochlrus
Sheepshead minnow, ELS
Cyprlnodon varlegatus
Sheepshead minnow, LC
Cyprlnodon varlegatus
tt * LC = life cycle or partial life
1
H
to
Species
Cladoceran,
Daphnla magna
Bluegi 1 1,
Lepomls macroch 1 rus
Sheepshead minnow.
FRESHWATER SPECIES
Technical 12.1-21.6 16
chlordane
Technical 1.22-2.20 1.6
ch lordane
SALTWATER SPECIES
Chlordane 7.1-17 1)
Chlordane 0.5-0.8 0.63
cycle, ELS = early life stage
Acute-Chronic Ratios
Acute Chronic
Value Value
Chemical (ug/l) (ug/l) Ratio
Technical 58 ]6 3.6
ch lordane
Technical 59 1.6 37
ch lordane
Chlordane 12.5 0.63 20
Cardwel 1, et al. 1977
Cardwel 1, et al. 1977
Parrlsh, et al. 1976
Parrlsh, et al. 1978
Cyprinodon varlegatus
-------
Table 3. Species wean acute values and acute-chronic ratios for chlordane
Rank*
Species
Species Mean
Acute Value
(lig/l)
FRESHWATER SPECIES
Species Mean
Acute-Chronic
Ratio
03
I
M
U)
14 Guppy,
Poecllla retlculata
13 Goldfish,
Carasslus auratus
12 Blueglll,
Lepomls roacrochlrus
11 CIadoceran,
Daphnla magna
10 Chinook salmon,
Oncorhynchus tshawytscha
9 Coho salmon,
Oncorhynchus klsutch
8 Brook trout,
Salvellnus fontlnalls
7 Scud,
Gammarus fasclatus
6 Fathead minnow,
Plmephales promelas
5 Scud,
Gammarus lacustrls
4 Rainbow trout,
Sal mo galrdnerl
Stonefly,
Pteronarcys calIfornica
Freshwater shrimp,
Palaemontes kadlakensls
190
82
59
58
57
56
45
40
37
26
25
15
37
3.6
6.3
-------
Table 3. (Continued)
CO
I
ink*
1
8
7
6
5
4
3
2
1
Species
Carp,
Cyprlnus carplo
SALTWATER
Threesplne stickleback,
Gasterosteus aculeatus
Sheepshead minnow,
Cyprlnodon varlegatus
Dungeness crab.
Cancer Register
Striped bass,
Morone saxatl 1 is
Plnflsh,
Lagodon rhomboldes
Eastern oyster,
Crassostrea virgin lea
Grass shrimp,
Palaemonetes pugio
Pink shrimp,
Species Mean
Acute Value
3
SPECIES
120
17.5
16.9
11.8
6.4
6.2
4.8
0.4
Species Mean
Acute-Chronic
Ratio
20
Penaeus duorarum
-------
Table 3. (Continued)
Ranked from least sensitive to most sensitive based on species mean
acute value.
Final Acute-Chronic Ratio = 14
Freshwater Final Acute Value - 2.4 v>g/l
Freshwater Final Chronic Value = 2,4 ug/l t- 14 = 0.17 ug/l
Saltwater Final Acute Value = 0.09 ug/l
Saltwater Final Chronic Value = 0.09 ug/l t- 14 = 0.0064 ug/l
Cd
I
M
Ul
-------
Table 4. Residues for chlordane
Species
Scud,
Hyal lela azteca
Fathead minnow,
Plmephales promelas
Sheepshead minnow
(juvenl le),
Cyprlnodon varlegatus
Sheepshead minnow
(adult),
Cypr l.nodon var 1 egatus
Sheepshead minnow
1 (juvenile),
H-1 Cyprlnodon vartegatus
Sheepshead minnow
(juvenl le),
Cyprlnodon varleqatus
Llpld
Tissue (<)
1 ' "•• —
Whole body
Whole body 7.6**
Whole body
Whole body 3.6***
Whole body
Whole body
B loconcentrat ion
Chemical Factor
FRESHWATER SPECIES
Technical 5,200*
Technical 37,800
ch lordane
SALTWATER SPECIES
Technical 10,300
chlordane
Technical 16,000
ch lordane
Technical 15,300
ch lordane
trans-Ch lordane 6,600
Duration
(days) Reference
65 Cardwel 1, et al. 1977
32 Velth, et al. 1979
28 Parrlsh, et hi. 1976
189 Parrlsh, et.al. 1978
28 Parrlsh, et al. 1978
28 Goodman, et al. 1978
percent composition In" technica.^hiord^:" pred°mlnant c°^t.tuents. Each constituent's b loconcentrat Ion adjusted for Its
** Percent llpld data from Velth, 1980.
***Percent llpld data from Hansen, 1980.
Maximum Permissible Tissue ConcentratIon
Action Level
Fish
Concentration
(mg/ka)
0.3
Reference
U.S. FDA Guide I Ine
7420.08, 1979
-------
Table 4. (Continued)
Geometric mean of normalized bloconcentratlon factors = 4,702
Marketability for human consumption: FDA action level for fish = 0.3 mg/kg
Percent llpid value for freshwater species (see Guidelines) - 15
Percent Jlpld value for saltwater species (see Guide!Ines) = 16
Freshwater: 0.3 0.0000043 mg/kg = 0.0043 ug/l
4,702 x 15
Saltwater: 0.3 = 0.0000040 mg/kg = 0.0040 ug/l
4,702 x 16
Freshwater Final Residue Value = 0.0043 ug/l
Saltwater Final Residue Value = 0.0040 ug/l
-------
Table 5. Other data for chlordane
apecles
Alga,
Scenedesmus quadrlcauda
Cladoceran,
Daphnla magna_
Cladoceran,
paphnla magna_
Tub If (eld worm,
Tublfex tub If ex
Tub 1 field worm,
Branch lura sower by 1
DO Scud.
1 Hyallela azteca
00 Scud,
Hyal lela azteca
Freshwater shrimp,
Palaemonetes kadlakensls
Freshwater shrimp,
Palaemonetes kadlakensls
Midge ( larva),
Chi ronomus^ p lumosus
Midge,
Chlronomus No. 51
Rainbow trout.
Sal mo galrdnerl
Rainbow trout,
Salmo galrdnerl
Chemical*
Technical
chlordane
Technical
ch lordane
Techn 1 ca 1
ch lordane
Ch lordane
Technical
chlordane
Techn 1 ca 1
chlordane
Techn 1 ca 1
ch lordane
Technical
ch lordane
Technical
ch lordane
Ch lordane
Techn 1 ca 1
ch lordane
Techn 1 ca 1
ch lordane
Ch lordane
Duration
FRESHWATER
7 days
96 hrs
7 days
24 hrs
72 hrs
168 hrs
65 days
24 hrs
120 hrs
24 hrs
25 days
5 hrs
24 hrs
Effect
•• — 111^,
SPECIES
Stimulated eel 1
division
LC50
Bloconcentrat Ion
of ch lordane =
3,800**
LC50
100? mortality
LC50
Reduced growth
and survival
LC50
LC50
LC50
Larval mortality
Death or distress
LCI 00
Resu It
(U9/I)
0.1
28.4
10,000
500
97.1
11.5
13.6
2.5
10
1.7
100
1,000
Reference
Gloosehenko 4 Lott
1977
Cardwel I, et a I. 1977
CardwelI, et al. 1977
Ludemann 4 Neumann,
1962
Naqvl, 1973
Cardwel I, et al. 1977
CardwelI, et al. 1977
Naqvi 4 Ferguson,
1970
Sanders, 1972
Ludemann 4 Neumann,
1962
CardwelI, et al. 1977
App legate, ot al.
1957
Ludemann 4 Neumann,
1961
-------
Table 5. (Continued)
03
I
H*
vo
Species
Rainbow trout,
Salmo galrdnerl
Brook trout,
Salveilnus fontlnalls
Northern pike,
Esox luclus
Fathead minnow,
Plmephales promelas
Green sunflsh,
Lepomls cyanellus
Channel catfish,
Ictalurus punctatus
Carp (fry),
Cyprlnus carp Io
Carp,
Cyprlnus carplo
Carp (fry),
Cyprlnus carplo
Largemouth bass,
Mlcropterus salmoIdes
Frog,
Bufo bufo
Chemical*
Chiordane
(emulsifI able
concentrate,
75* A.I.)
TechnIcaI
chlordane
Chlordane
TechnIcaI
ch lordane
Chlordane
(emulsiflable
concentrate,
75* A.I.)
Chlordane
Chlordane
(emulsif lable
concentrate,
72? A.I.)
Chlordane
Chlordane
(emulsif lable
concentrate,
72* A.I.)
Chlordane
47.2$ A.I.
Chlordane
Duration
24 hrs
13 raos
24 hrs
11 mos
<35 mln
96 hrs
91 hrs
Effect
60% mortality
Reduced embryo
viability
LCI 00
Result
(tig/1) Reference
250
Mayhew, 1955
0.32 Cardwell, et al. 1977
50 Ludemann & Neumann,
1961
Survival, growth, >6.03
reproduction
Cardwell, et al. 1977
Avoidance 5,000 Summerfelt & Lewis,
1967
LD50 500 Clemens 4 Sneed, 1959
Accelerated 1.0 Malone & Blaylock,
development 1970
48 hrs LC50 1,160
96 hrs 93.7? mortality 5,000
33 hrs Increased oper-
cular rate
24 hrs
LC50
30
2,000
Ludemann & Neumann,
I960
Malone & Blaylock,
1970
Morgan, 1975
Ludemann & Neumann,
1962
-------
Table 5. (Continued)
ro
i
to
o
Species
Nature I phy top I ankton
community
Eastern oyster,
Crassostrea virgin lea
Eastern oyster,
Crassostrea virgin lea
Brown shrimp,
Penaeus aztecus
Pink shrimp,
Penaeus duorarum
Grass shrimp,
Palaemonetes puglo
Blue crab,
Ca111nectes sap Idus
Oungeness crab (zoeae),
Cancer maglster
Oungeness crab,
Cancer maglster
Dungeness crab,
Cancer maglster
Dungeness crab,
Cancer maglster
Sheepshead minnow,
CyprInodon varIegatus
Sheepshead minnow,
CyprInodon varIegatus
Chemical*
Ch lordane
Ch lordane
Ch lordane
Ch lordane
Ch lordane
Ch lordane
Ch lordane
Ch lordane
Ch lordane
Ch lordane
Ch lordane
Ch lordane
Ch lordane
Duration
SALTWATER
4 hrs
24 hrs
96 hrs
48 hrs
96 hrs
96 hrs
48 hrs
96 hrs
>70 days
>70 days
90 days
96 hrs
96 hrs
Result
Effect (up/I)
SPECIES
94 jt decrease In 1,000
productivity
Growth affected 10
Bloconcentratlon
factor = 5,522
EC50 4.4
Bloconcentratlon
factor = 4,564
Bloconcentratlon
factor = 2,117
EC 50 480
LC50 >10
50* larval 0.15
mortality In 37 days,
retardation of
molting
No effect 0.015
Survival not 1
affected
Bloconcentratlon
factor = 15,250
Bloconcentratlon
Reference
Butler, 1<
Butler, e1
Parrlsh, «
Butler, \(.
Parrlsh, e
Parrlsh, t
Butler, IS
Caldwel 1,
Cat dwell,
Cal dwell.
Cal dwell.
Parrlsh, e
Schlmmel ,
1976a
-------
W
I
NJ
H-1
Table 5. (Continued)
Species
Plnflsh,
Lagodon rhomboldes
Spot,
Lelostomus xanthurus
Spot,
Lelostomus xanthurus
White mul let,
Mug 1 1 curema
Chemical*
Ch lordane
Ch lordane
Ch lordane
Ch lordane
Duration
96 hrs
96 hrs
72 hrs
48 hrs
Result
Effect (ug/D
Bloconcentratlon
factor = 6,227
Bloconcentratlon
factor = 9,250
Bloconcentratlon
factor = 4,600
LC50 5.5
Reference
Parrlsh, at al. 1976
Schlnroel, et al.
1976a
Schimmel , et al.
1976b
Butler, 1963
"Adjusted for wet weight. Total of the seven predominant constituents. Each constituent's bloconcentration
adjusted for Its percent composition In technical chlordane.
-------
REFERENCES
Applegate, V.C., et al.- 1957. Toxicity of 4,346 chemicals to larval lamp-
reys and fishes. U.S. Dept. Inter. Fish Wild!. Serv. Rep. 207.
Butler, p.A. 1963. Commercial Fisheries Investigations. In: Pesticide and
Wildlife Studies. A Review of Fish and Wildlife Service Investigations dur-
ing 1961 and 1962. U.S. Fish Wild!. Serv. Circ. 167: 11.
Butler, p.A., et al. 1960. Effect of pesticides on oysters. Proc. Shell-
fish Assoc. 51: 23.
Caldwell, R.S. 1977. Biological effects of pesticides on the Dungeness
crab. EPA 600/3-77-131: 1. U.S. Environ. Prot. Agency, Cincinnati, Ohio.
Cardwell, R.D., et al. 1977. Acute and chronic toxicity of chlordane to
fish and invertebrates. EPA 600/3-77-019. EPA Ecol. Res. Ser., U.S. Envi-
ron. Prot. Agency, Duluth, Minnesota.
Clemens, H.P. and K.E. Sneed. 1959. Lethal doses of several commercial
chemicals for fingerling channel catfish. U.S. Fish Wild!. Serv. Spec. Sci.
Rep. Fish No. 316: 10.
Glooschenko, V. and J.N.A. Lott. 1977. Effects of chlordane on green algae
Scenedesmus quadricauda and Chlomydomonas. Can. Jour. Bot. 55: 2866.
B-22
-------
Goodman, L., et al. 1978. Effects of heptachlor and toxaphene on labora-
tory-reared embryos and fry of the sheepshead minnow. Proc. 30th Annu.
Conf. S.E. Assoc. Game jjish. Comrn.
Hansen, 0. 1980. Memorandum to C.E. Stephan. U.S. EPA. August, 1980.
Henderson, C., et al. 1959. Relative toxicity of ten chlorinated hydrocar-
bon insecticides to four species of fish. Trans. Am. Fish. Soc. 8: 23.
Katz, M. 1961. Acute toxicity of some organic insecticides to three spe-
cies of salmonids and to the threespine stickleback. Trans. Am. Fish. Soc.
90: 264.
Korn, S. and R. Earnest. 1974. Acute toxicity of twenty insecticides to
striped bass, Morone saxatilis. Calif. Fish Game. 60: 128.
Ludemann, D. and H. Neumann. 1960. Versuche uber die akute toxische
Wirkung neuzeitlicher Kontaktinsektizide auf einsommerige Karpfen (Cyprinus
carpio L.). [Acute toxicity of modern contact insecticides to carp (Cy_-
prinus carpio L.] Z. Angew. Zoo!. 47: 11.
Ludemann, D. and H. Neumann. 1961. Versuche uber die akute toxische Wirk-
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of modern contact insecticides for freshwater animals.) Z. Angew. Zool.
48: 87.
B-23
-------
Ludemann, D. and H. Neumann. 1962. Uber die Wirkung der neuzeitlichen Kon-
taktinsektizide auf die Tiere des Susswassers. Anz. Schaedliingskd Pifan-
zen-Umweltschutz. 35: ~§.
Macek, K.J., et al. 1969. The effects of temperature on the susceptibility
of bluegills and rainbow trout to selected pesticides. Bull. Environ. Con-
tarn. Toxicol. 4: 174.
Malone, C.R. and B.G. Blaylock. 1970. Toxicity of insecticide formulations
to carp embryos reared in vitro. Jour. Wild!. Manage. 34: 460.
Mayhew, J. 1955. Toxicity of seven different insecticides to rainbow trout
Salmo gairdnerii (Richardson). Proc. Iowa Acad. Sci. 62: 599.
Mehrle, P.M., et al. 1974. Nutritional effects on chlordane toxicity in
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Morgan, W.S.G. 1975. Monitoring pesticides by means of changes in electric
potential caused by fish opercular rhythms. Prog. Water Technol. 7: 33.
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worm Branchiura sowerbyi from the Mississippi delta. Jour. Econ. Ent.
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Naqvi, S.M. and D.E. Ferguson. 1970. Levels of insecticide resistance in
freshwater shrimp, Palaemonetes Icadiakensis. Trans. Am. Fish. Soc. 4: 696.
B-24
-------
Parrish, P.R., et al. 1976. Chlordane: Effects on several estuarine organ-
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freshwater fish Cyprinus carpio. Ind. Jour. Environ. Health. 17: 140.
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costracan crustaceans. U.S. Dept. Inter. Fish Wild!. Tech. Pap. 66.
Sanders, H.O. and O.B. Cope. 1968. The relative toxicities of several pes-
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Schimmel, S.C., et al. 1976a. Heptachlor: Toxicity to and uptake by sev-
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Schimmel, S.C., et al. 1976b. Heptachlor: Uptake, depuration, retention,
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Toxicol. Environ. Health. 2: 169.
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B-26
-------
Mammalian Toxicology and Human Health Effects
EXPOSURE
Ingestion from Water -
The lowest detectable concentrations for a number of chemi-
cals were reviewed, and it was concluded that the limit for chlor-
dane is 1 ug/1 for an analyst using standardized procedures, with
0.3 ug/1 being the most sensitive detection level using more
sophisticated techniques (Ballinger, personal communication). By
using unusually large quantities of sample and concentration mea-
sures, the sensitivity may be increased.
A study of the persistence of technical chlordane in river
water showed 85 percent remaining after eight weeks (Eichelberger
and Lichtenberg, 1971). of the major components of technical
chlordane, cis- and trans-chlordane were completely stable over
the 8-week period. All but two of the remaining components were
at least partially changed.
Schafer, et al. (1969) examined over 500 grab samples from
water supplies of the Mississippi and Missouri Rivers. Chlordane
was detected in over 20 percent of the finished waters, with the
maximum concentration being 8 ug/1. An extensive search of the
literature and U.S. EPA reports generated from the Agency's ana-
lytical activities resulted in a list of organic compounds in
drinking water of the United States (U.S. EPA, 1975). The highest
concentration reported for chlordane did not exceed that reported
by Schafer, et al. (1969). Chlordane has also been detected in
rainwater (Bevenue, et al. 1972; 41 FR 7552).
C-l
-------
Although reports occasionally are received of individual
household wells becoming contaminated after a house is treated
with chlordane for termite control, only one report has been pub-
lished of the contamination of a municipal water system (Harring-
ton, et al. 1978). On March 24, 1976 a section of the public
water system supplying 105 persons in Chattanooga, Tenn. became
contaminated. Back siphonage apparently occurred while diluting a
chlordane concentrate with a hose during a period of negative
pressure. Of the 71 residents affected, 13 had symptoms of mild
acute chlordane toxicity. None of the residents has had prolonged
sequelae from the exposure.
Ingestion from Food
The Food and Drug Administration (FDA) has been systemati-
cally monitoring chlordane in the food supply of the United States
since 1965. Chlordane has been found infrequently during the 11
years of survey (Nisbet, 1976). The only quantifiable sample col-
lected was 0.059 mg/kg measured in a sample of grain in 1972
(Manske and Johnson, 1975). In the most recent published results
chlordane was not detected, even in trace amounts (Johnson and
Manske, 1977). Nisbet (1976) discussed the problems of composit-
ing and analytical methods. Residues of technical chlordane are
multi-component, so that the practical detection limit is several
times higher than the 0.003 mg/kg stated for single components.
Using data from FDA and others, Nisbet calculated an average
chlordane intake from fish of 1 ug/day and concluded that fish
represent the most significant dietary exposure to chlordane.
C-2
-------
A bioconcentration factor (BCF) relates the concentration of
a chemical in aquatic animals to the concentration in the water in
which they live. The steady-state BCFs for a lipid-soluble com-
pound in the tissues of various aquatic animals seems to be pro-
portional to the percent lipid in the tissue. Thus, the per
capita ingestion of a lipid-soluble chemical can be estimated from
the per capita consumption of fish and shellfish, the weighted
average percent lipids of consumed fish and shellfish, and a
steady-state BCF for the chemical.
Data from a recent survey on fish and shellfish consumption
in the United States was analyzed by SRI International (U.S. EPA,
1980). These data were used to estimate that the per capita con-
sumption of freshwater and estuarine fish and shellfish in the
United States is 6.5 g/day (Stephan, 1980). In addition, these
data were used with data on the fat content of the edible portion
of the same species to estimate that the weighted average percent
lipids for consumed freshwater and estuarine fish and shellfish is
3.0 percent.
Two laboratory studies, in which percentage of lipids and a
steady-state BCF were measured, have been conducted on chlordane.
The mean of the BCF values, after normalization to 1 percent lip-
ids, is 4,707 (see Table 5 in Aquatic Life Toxicology, Section B).
An adjustment factor of 3 can be used to adjust the mean normal-
ized BCF to the 3.0 percent lipids that is the weighted average
for consumed fish and shellfish. Thus, the weighted average bio-
concentration factor for chlordane and the edible portion of all
freshwater and estuarine aquatic organisms consumed by Americans
is calculated to be 14,100.
C-3
-------
The National Academy of Sciences (NAS, 1977) in reviewing the
results of Moore (1975) reported that of 200 samples of milk col-
lected in Illinois during the period 1971-1973, 87 percent were
positive for chlordane. The average concentration was 50 ug/1.
Cyclodienes, such as chlordane, apparently are ingested with for-
age and tend to concentrate in lipids. Oxychlordane, a major mam-
malian metabolite of chlordane and heptachlor, was found in 46
percent of 57 human milk samples collected during 1973-1974 in
Arkansas and Mississippi. The mean value was 5 ug/1 and the maxi-
mum was 20 ug/1 (Strassman and Kutz, 1977).
Inhalation
in a survey of the extent of atmospheric contamination by
pesticides, air was sampled at nine localities representative of
both urban and agricultural areas. At least one chlorinated pes-
ticide was found at all locations, but chlordane was not found in
any samples (Stanley, et al. 1971). In a larger survey summarized
by Nisbet (1976), 2,479 samples were collected at 45 sites in 16
states. Chlordane was detected in only two samples, with concen-
trations of 84 and 204 ng/m^.
Dermal
Chlordane can be absorbed through the skin and produce toxic
effects (Gosselin, et al. 1976). Dermal exposure would be ex-
pected to occur only with occupational manufacture or use of the
pesticide. Absorption can range from negligible to that producing
acute effects, depending on the degree of exposure. For the gen-
eral population, dermal exposure would be negligible. Persons
using chlordane could have the pesticide persist on their skin for
C-4
-------
long periods. In one study, hexane rinsings of the hands of a
former pest control operator contained chlordane two years after
his last known exposure (Kazen, et al. 1974) .
PHARMACOKINETICS
Absorption
Cis- and trans-chlordane are the primary components of the
insecticide. Both are stable when held under ambient conditions
or mixed with the feed of experimental animals. A single oral
dose of chlordane administered to rats resulted in approximately 6
percent absorption (Barnett and Dorough, 1974). Small daily doses
result in greater absorption values approximating 10 to 15 per-
cent. Feeding the pure cis- and tra-ns-isomers separately indi-
cates that the cis- isomer is more effectively eliminated from the
rats than the trans-isomer. Although the difference is not exten-
sive, the data indicate that in long-term exposure situations,
trans-chlordane would contribute a relatively greater amount to
the body burden of the exposed animal than would the cis-isomer.
Distribution
Barnett and Dorough (1974) also studied the distribution of
chlordane and metabolites in rats using radioactive carbon. The
levels of residues in the tissues were generally low, except in
the fat. Levels of chlordane residues in the fat of the rats,
after being fed 1, 5, and 25 mg/kg in their diet for 56 days, were
approximately three times the concentration in the diet. Concen-
trations in the liver, kidney, brain, and muscle were 12, 10, 4,
and 2 percent, respectively, of the concentration in the feed.
C-5
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Once the chlordane was removed from the diet, all residues
declined steadily for four weeks, at which time the concentrations
were reduced approximately 60 percent. During the following four
weeks, the residues declined only slightly. Treatment with trans-
chlordane resulted in higher concentrations of residues in the
tissues than did treatment with the cis-isomer.
Dorough and Hemken (1973) fed three levels of chlordane to
cows for 60 days and tested the milk periodically. Milk levels of
chlordane and the metabolite oxychlordane increased sharply the
first week and more slowly thereafter. When chlordane was removed
from the diet, the milk residues dropped rapidly during the week
following termination of treatment and stabilized after two
weeks.
Metabolism
Polen, et al. (1971) and Street and Blau (1972) found oxy-
chlordane to be a mammalian metabolite of chlordane, and to per-
sist in adipose tissue. Street and Blau (1972) observed that the
toxicity of oxychlordane was greater than the parent compound.
Barnett and Dorough (1974) tentatively identified several hydroxy-
lated metabolites of chlordane in rat excreta in addition to oxy-
chlordane and concluded that the metabolism of chlordane takes
place via a series of oxidative enzyme reactions.
Tashiro and Matsumura (1977) attempted to isolate and posi-
tively identify the metabolic by-products of chlordane to estab-
lish the route of its metabolism. The major route of metabolism
for both cis- and trans-chlordane is via dichlorochlordene and
oxychlordane. These metabolic intermediates are further converted
C-6
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to two key metabolites, l-exo-hydroxy-2-chlorochlordene and 1-exo-
hydroxy-2-endo-chloro-2,3-exo-epoxychlordene, which are readily
degraded further. ITrans-chlordane is more readily metabolized
through this route.
There is yet another major metabolic route for cis-chlordane
which involves more direct hydroxylation reactions to form 1-exo-
hydroxydihydrochlordenes and 1, 2-trans-dihydroxydihydrochlordene.
Cis-chlordane is more readily degraded through this latter route.
As judged by a toxicity test on mosquito larvae, none of the meta-
bolic end products appear to be more toxic than the original
chlordanes or the intermediates.
Excretion
Most chlordane is excreted in the feces of rats. Only about
6 percent of the total intake is voided in the urine. Rabbits,
however, provide a different pattern. Urinary elimination of
chlordane in rabbits is greater than excretion in the feces. Nye
and Dorough (1976) suggest that the conjugative metabolism system
is more efficient in rabbits than in rats. The patterns of excre-
tion following inhalation of chlordane by rats follow the patterns
reported for oral administration (Nye and Dorough, 1976).
Human half-life data were obtained when chlordane was acci-
dently ingested by a young boy (Curley and Garrettson, 1969). A
whole body value of 21 days was calculated, which is long compared
to drugs used in therapy, but quite short when compared to other
chlorinated insecticides. This compares to a half-life of about
23 days obtained by Barnett and Dorough (1974) in studies with
rats fed chlordane for 56 days. After the levels reached 60 per-
C-7
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cent, further reduction was slight. Serum half-life of chlordane
in a young girl was found to be 88 days by Aldrich and Holmes
(1969) .
EFFECTS
Acute, Subacute, and Chronic Toxicity
Human toxicity data for chlordane usually is obtained after
accidental exposure to the compound. Curley and Garrettson (1969)
reported that shortly after a 20-month-old boy accidently drank an
unknown amount of chlordane, he vomited and began a series of con-
vulsions lasting 3 to 5 minutes each. After being given 14 mg/kg
body weight phenobarbital, the seizures stopped. Body temperature
rose to 102°F and then gradually decreased to normal. At no time
was there evidence of pulmonary disease. Neurological examination
at the time seizures were occurring revealed brisk deep tendon re-
flexes in all extremities. Cranial nerve function was intact and
nystagmus was absent. An EEG taken 48 hours after exposure was
normal. Three months after exposure, all tests appeared normal.
Similar cases were reported by Dadey and Krammer (1953) and Aid-
rich and Holmes (1969). Barnes (1967) reported that intermittent
dermal exposure of a nursery worker to chlordane as a soil insec-
ticide produced symptoms including repeated seizures, electro-
encephalographic dysrhythmia, convulsions, and twitching. After
cessation of contact with chlordane, all symptoms disappeared.
Purified chlordane at a concentration of 100. ug/1 was re-
ported to induce cytotoxic effects in human HeLa cell cultures by
inhibiting growth and altering cell morphology (Gabliks, 1965).
C-8
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A number of studies have been conducted to determine chlor-
dane LD50 values for laboratory animals. Claude, et al.
(1976) reported the oral LD50 of chlordane to be 350 mg/kg in
rats, 390 mg/kg in mice, and 1,720 mg/kg in hamsters. Studies by
Harbison (1975) showed the intraperitoneal LD50 of analytical
chlordane to be 343 mg/kg for the adult rat, 1,121 mg/kg for new-
born rats, and 539 mg/kg for newborn rats pretreated with 40 mg/kg
sodium phenobarbital. Ben-Dyke, et al. (1970) reported an oral
LD50 value of 283 mg technical grade chlordane/kg body weight
for the rat. Ambrose, et al. (1953) reported a chlordane oral
LD50 value of 590 mg/kg for the rat. Daily oral doses of 25
mg/kg or less for 15 days produced no toxic symptoms.
A review of the literature by the National Institute for Oc-
cupational Safety and Health (NIOSH, 1976) indicated a range of
chlordane LD50 values from 100 mg/kg for rabbits with oral
administration to 700 mg/kg for rats with dermal administration.
Gaines (1960) reported technical grade chlordane oral LD50
values of 335 mg/kg for male rats and 430 mg/kg for females and a
dermal LD50 of 530 mg/kg for the female rat. The National
Academy of Sciences (1977) reported dermal LD50 values of 840
and 690 mg/kg for male and female rats, respectively. Chlordane
fed to rats at 2.5 mg/kg in the diet caused slight liver damage.
Wazeter, et al. (1968) reported acute oral LD50 values of
392 mg/kg, 327 mg/kg, and 371 mg/kg for cis(alpha)chlordane,
trans(gamma)chlordane, and an equal mixture of the two isomers,
respectively, in the male rat. Thus, the data indicate that tech-
nical grade chlordane and the individual purified chlordane iso-
C-9
-------
mers exhibit approximately equal toxicity. Boyd and Taylor (1969)
observed that chlordane toxicity is increased in rats fed low pro-
tein diets. Oral LD50 values for reference grade technical
chlordane ranged from 137 mg/kg for rats fed a low protein diet,
to 311 mg/kg for rats fed a normal protein diet.
Mice receiving 0.075 and 0.15 mg of cis- or trans-chlordane
on days 2, 3, and 4 of life exhibited a delay in general matura-
tion (Talamantes and Jang, 1977). Chlordane administered at 25 to
75 mg/kg in the Indian desert gerbil produced hyperglycemia and
lowered the glucose tolerance, indicating an impairment in the up-
take and utilization of glucose (Saxena and Karel, 1976). Re-
peated doses of 2.5 mg/kg chlordane to these animals produced
changes in serum proteins, blood glucose, and alkaline and acid
phosphatase activity (Karel and Saxena, 1976). The no-effect
level, as indicated by induction of microsomal liver enzymes in
male rats receiving chlordane in their diets over two weeks, was 5
mg/kg (Den Tonkelaar and Van Esch, 1974).
Hyde and Falkenberg (1976) studied neuroelectrical distur-
bances in rats as a result of injections of chlordane. Intraperi-
toneal injection of 350 mg/kg resulted in mild tremors and disori-
entation within a few minutes and death in one hour. Daily injec-
tion of 0.15, 1.75, and 25 mg/kg in adult rats resulted in dose-
dependent alterations of brain potentials without behavioral signs
of chronic toxicity. Changes were directly related to length of
exposure, indicating that chlordane may be a cumulative neuro-
toxin.
C-10
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Mammalian metabolism of the chlordane isomers results in the
formation of the toxic metabolite oxychlordane (Street and Blau,
1972; Barnett and Borough, 1974). Oxychlordane has been demon-
strated to be approximately 20 times more toxic than the parent
compound, with an acute oral LD5Q value of approximately 19
mg/kg in male and female rats (Mastri, et al. 1969). Furthermore,
oxychlordane has been demonstrated to be the most persistent
metabolite stored in rat adipose tissue (Street and Blau, 1972).
The other products of chlordane isomer metabolism in rats are much
less toxic (Mastri, et al. 1969).
Synergism and/or Antagonism
Histologic slides prepared from rats pretreated with 25 mg/kg
chlordane and then injected with 0.5 ml of a 25 percent solution
of carbon tetrachloride in olive oil, revealed more extensive
hepatocellular necrosis in the chlordane-pretreated rats than was
found in the carbon tetrachloride treatment alone (Stenger, et al.
1975).
Ludke (1976) found that quail, treated with chlordane fol-
lowed by endrin, had considerably more chlordane residues in their
brains than did birds treated with chlordane alone, suggesting an
increased uptake of chlordane in brains of birds post-treated with
endrin. Quail pretreated with 10 mg/kg chlordane exhibited de-
creased susceptibility (antagonism) to parathion but not to para-
oxon dosage, as measured by cholinesterase activity (Ludke,
1977).
C-ll
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Teratoqenicity
Chlordane was found not to be teratogenic in rats when fed at
concentrations of 150 to 300 mg/kg in the diet during pregnancy
(Ingle, 1952).
Mutagenicity
Arnold, et al. (1977) administered chlordane to Charles River
CD-I male mice in a single dose of 50 or 100 mg/kg. The males
were subsequently mated with untreated female mice. No dominant
lethal changes were produced. Studies by Ahmed, et al. (1977)
with the SV-40 transformed human fibroblast cell line VA-4 showed
that chlordane induced unscheduled DNA synthesis, indicating that
chlordane is a potential genotoxic agent. Metabolic activation
eliminated the induction of unscheduled DNA synthesis. Simmon, et
al. (1977) found that neither pure cis-chlordane nor trans-chlor-
dane were mutagenic in the Ames Salmonella microsome assay. Tech-
nical grade chlordane, however, was found to be mutagenic in Sal-
monella typhimurium strains TA 1535, TA 98 and TA 100. An S-9
liver activation mix did not enhance the mutagenic activity.
Carcinogenicity
A retrospective epidemiological study of 1,403 workers em-
ployed in the manufacture of chlordane and heptachlor showed no
statistically significant excess cancer mortality (Wang and Mac-
Mahon, 1979a). Cancer of the lung was the only tumor type found
in excess of expected values, and the excess was not associated
with duration of exposure or latency in such a way as to suggest
an etiologic relationship between the lung cancer and occupational
exposure to heptachlor and chlordane. It should be noted that
C-12
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the authors considered the study population size too small and the
period of follow-up too short to translate these negative findings
into a statement that there is not excess risk of cancer asso-
ciated with heptachlor and chlordane exposure in man (Wang and
MacMahon, 1979a).
In their study of manufacturing workers, Wang and MacMahon
(1979a) did note a substantial and statistically significant ex-
cess of deaths due to cerebrovascular disease. This excess was
not seen, however, in their prospective epidemiological study of
16,126 pesticide applicators Wang and MacMahon (1979b). This
cohort included "termite control operators" (TCOs) who would be
expected to have had exposures to chlordane and heptachlor in
excess of the general population. Although TCOs showed no statis-
tically significant excess of cancer relative to expected values,
Wang and MacMahon (1979b) noted that their study was limited as it
related to cancer experience, since relatively few workers had
substantial work experience and could be followed for long periods
after first employment.
A dose-dependent incidence of hepatocellular carcinoma in
male and female strain B6C3F1 mice fed diets containing analytical
grade chlordane was reported by the National Cancer Institute
(NCI, 1977), and the results of their investigation are summarized
in Table 1. This bioassay of chlordane for possible carcinogeni-
city was conducted by Gulf South Research Institute under contract
to the National Cancer Institute. The batch tested contained 71.7
percent cis-chlordane, 23.1 percent trans-chlordane, 0.3 percent
C-13
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TABLE 1
Liver Carcinomas in Mice Associated With the
Oral Feeding of Chlordane
Dose (ppm)
63.8
56.2
50
30.1
29.9
25
5
0 (controls)
0 (controls)3
% Positive (No. Tested)-1- % Positive (No. Tested)2
Male Female Male Female
69(49)
88(49)
82(39) 70(37)
6(47)
33(48)
79(52) 64(50)
9(55) 0(61)
11(18) 0(19) 9(33) 0(45)
18(92) 4(78)
(1) National Cancer Institute, 1977
(2) Epstein, 1976
(3) Pooled controls consisted of matched controls combined with
other untreated mice.
C-14
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heptachlor, 0.6 percent nonachlor, 1.1 percent hexachlorocyclo-
pentadiene, 0.25 percent chlordene isomers, and 2.95 percent un-
specified chlorinated compounds. The material was incorporated
into the feed of B6C3F1 hybrid mice.
Groups of 50 mice of each sex at 35 days of age were admin-
istered the test material at two concentrations for 80 weeks and
then observed for 10 weeks. Matched controls were used during the
tests. Since similar bioassays were conducted on five other com-
pounds, the results were also given for the pooled controls.
Hepatocellular carcinoma showed a highly significant dose-related
trend for the mice. Male mice fed a time-weighted average concen-
tration of 56.2 mg/kg chlordane in the diet for 80 weeks exhibited
an 87.8 percent (43/49) incidence of liver tumors, compared with
an 11.1 percent (2/18) incidence in matched male controls and an
18.5 percent (17/92) incidence in pooled male controls from other
experiments. In the same investigation, males fed a time-weighted
average concentration of 29.9 mg/kg chlordane in the diet for 80
weeks exhibited a 33.3 percent (16/48) incidence of liver tumors.
Female mice fed a time-weighted average concentration of 63.8
mg/kg chlordane in the diet for 80 weeks exhibited a 69.4 percent
(34/49) incidence of liver tumors, as compared with a 0 percent
(0/19) incidence in matched female controls and a 3.8 percent
(3/78) incidence in pooled female controls from other experiments.
Female mice fed a time-weighted average concentration of 30.1
mg/kg chlordane in the diet for 80 weeks exhibited a 6.4 percent
(3/47) incidence of liver tumors.
C-15
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Similar studies were conducted by Gulf South with analytical
grade chlordane, using Osborne-Mendel strain rats. Groups of 50
rats of each sex were administered low or high concentrations for
80 weeks and then observed for 29 weeks. Time-weighted average
doses used for the male rats were 203.5 and 407.0 rag/kg, while the
female rats received 120.8 and 241.5 mg/kg. The effects of chlor-
dane on body weights and other clinical signs indicated that the
dosages used were near the maximum permissible. In contrast to
findings with mice, hepatocellular carcinomas failed to appear at
a significant rate of incidence in rats administered chlordane.
Further, the number of lesions of the liver in rats did not become
significant with the inclusion of nodular neoplasia or with the
application of life-table adjustment to the data.
In another bioassay, the International Research and Develop-
ment Corp. (IRDC), using Analytical Reference Standard Chlordane
(Technical), fed groups of 100 male and 100 female Charles River
CD-I mice dietary levels of 5, 25, and 50 mg/kg food. Feeding
commenced at six weeks of age and continued for 18 months (Ep-
stein, 1976). The IRDC report, reviewed by Epstein, made no
inference and drew no conclusion regarding carcinogenicity, in
spite of its conclusion that chlordane induced a statistically
significant increase of nodular hyperplasias in the 25 and 50
mg/kg groups. The report also noted an increased incidence of
hepatomas in the male 5 and 25 mg/kg groups. Epstein also re-
viewed the data of Reuber, who conducted a histological re-evalua-
tion of the IRDC slides and found that most of the histological
material designated by IRDC as nodules were in fact carcinomas of
C-16
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the liver. Reuber's diagnoses were corroborated by three other
independent pathologists and are summarized in the previous
Table 1. Thus, chlordane was found to produce liver cancer in
both sexes of two different strains of mice.
Becker and Sell (1979) recently reported an elevated inci-
dence of hepatic alterations in C57BL/6N male mice that were given
25 and 50 ppm chlordane in their diet. (The chlordane used was
greater than 90 percent heptachlor.) Both primary hepatocellular
carcinomas and "benign proliferative lesions" were seen in the
treated animals; animals receiving the control diet developed
neither histological alterations of the liver nor gross tumors.
The total absence of tumors in the controls was not surprising in
view of the fact that the C57BL/6N mouse has been reported to
demonstrate virtually no spontaneous tumors of the liver and to
require substantial exposure to known carcinogens for the produc-
tion of tumors (Becker and Sell, 1979). This observation was
borne out by the findings of Becker and Sell upon dietary adminis-
tration of 0.045 or 0.03 percent acetylaminofluorene (AAF) to the
C57BL/6N mouse. While both primary hepatocellular carcinomas and
benign proliferative lesions were seen with AAF, the incidence
associated with this demonstrated animal carcinogen was relatively
low; in fact, it was lower than the incidence associated with
chlordane treatment.
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CRITERION FORMULATION
Existing Guidelines and Standards
The American Conference of Governmental industrial Hygienists
(ACGIH, 1977) adopted a time-weighted average value of 0.5 mg/m
for chlordane based on inhalation exposure. The short-term expo-
sure limit (15 minutes) was set at 2 mg/m3.
An acceptable daily dose for man has been estimated to be
0.001 mg/kg body weight (Food Agric. Organ., 1968). Although a
limit of 3 ug/1 was originally suggested for chlordane under the
proposed Interim Primary Drinking Water Standards (40 FR 11990),
the final U.S. EPA regulations (40 FR 59566) did not include a
limit in view of the cancellation proceedings under the Federal
Insecticide, Fungicide, and Rodenticide Act (40 FR 59566). Cana-
dian Drinking Water Standards (Dept. Natl. Health Welfare, 1968)
list a tentative maximum permissible limit for chlordane of 3
ug/1, which is applicable to raw water supplies in Canada.
Current Levels of Exposure and Special Groups at Risk
Nisbet (1976) estimated total daily intake of chlordane from
all possible sources by back-calculating from the level of oxy-
chlordane stored in tissue. A value of 9 ug/day chlordane intake
was obtained. Nisbet also identified highly exposed segments of
the general population: children as a result of milk consumed;
fishermen and their families because of the high consumption of
fish and shellfish, especially freshwater fish; persons living
downwind from treated fields; and persons living in houses treated
with chlordane pesticide control agents.
C-18
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Basis and Derivation of Criterion
Several approaches are available to estimate a criterion
level for chlordane in ambient water. Using the Food and Agricul-
tural Organization/World Health Organization (FAO/WHO) value of
0.001 mg/kg of body weight as the maximum daily human intake, and
assuming an average body weight of 70 kg, the allowable intake
would be 70 ug/day. Further, subtracting Nisbet's (1976) value of
9 ug as the daily intake from fish, shellfish, milk, inhalation,
etc., and assuming that the contribution from drinking water is a
negligible part of this value, the ambient water criterion becomes
61 ug/day. At 2 I/day consumption, the maximum allowable concen-
tration would be 30 ug/1.
The proposed U.S. EPA drinking water regulations (40 FR
11990), the Canadian standards, and the National Technical Advis-
ory Committee (Fed. Water Pollut. Control Admin., 1968) all sug-
gest a chlordane limit of 3 ug/1 for drinking water. The latter
report specifically indicates that the water treatment process has
little effect on chlordane.
Although there are limitations to the procedure, the indus-
trial inhalation exposure limit of the American Conference of
Governmental Industrial Hygienists (1977) may be converted to a
limit for ingestion (Stokinger and Woodward, 1958). Assuming ab-
sorption via the GI tract for chlordane is one-fifth the absorp-
tion by inhalation:
mg 10m3 5 day work week 1
x x - - x - = 0.7 mg/day.
workday 7 day/wk
C-19
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Consumption of 2 liters of water daily and the consumption of
6.5 g of contaminated fish which have a bioconcentration factor of
14,100 result in a -maximum permissible concentration of 7.5 ug/1
for the ingested water.
The use of inhalation data assumes an 8-hour day, time-
weighted average occupational exposure in the working place with
workers inhaling the toxic substance throughout such a period.
Exposures for the general population should be considerably less.
Such worker-exposure inhalation standards are inappropriate for
the general population, since they presume an exposure limited to
an 8-hour day, an age bracket of the population that excludes the
very young and the very old, and a healthy worker prior to expo-
sure. Ingestion data is superior to inhalation data when the
risks associated with the food and water of the water environment
are being considered.
Under the Consent Decree in NRDC v. Train, criteria are to
state "recommended maximum permissible concentrations (including
where appropriate, zero) consistent with the protection of aquatic
organisms, human health, and recreational activities." Chlordane
is suspected of being a human carcinogen. Because there is no
recognized safe concentration for a human carcinogen, the recom-
mended concentration of chlordane in water for maximum protection
of human health is zero.
Because attaining a zero concentration level may be infea-
sible in some cases and in order to assist the Agency and states
in the possible future development of water quality regulations,
the concentrations of chlordane corresponding to several incre-
C-20
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mental lifetime cancer risk levels have been estimated. A cancer
risk level provides an estimate of the additional incidence of
cancer that may be expected in an exposed population. A risk of
ID'5, for example, indicates a probability of one additional
case of cancer for every 100,000 people exposed, a risk of
10-6 indicates one additional case of cancer for every million
people exposed, and so forth.
In the Federal Register notice of availability of draft ambi-
ent water quality criteria, EPA stated that it is considering set-
ting criteria at an interim target risk level of 1Q-5,
10"6, or 10~7 as shown in the table below.
Exposure Assumptions Risk Levels
(Per day.) and Corresponding Criteria (1)
£ 10-7 1Q-6 10-5
2 liters of drinking o 0.046 ng/1 0.46 ng/1 4.6
water and consumption
of 6.5 g fish and
shellfish. (2)
and ° °-048 ng/l °-48 ng/i 4-8
(1) Calculated by applying a linearized multistage model, as
discussed in the Human Health Methodology Appendices to
the October 1980 Federal Register notice which announced
the availability of this document, to the animal bio-
assay data presented in Appendix and in Table 1. since
the extrapolation model is linear at low doses, the
additional lifetime risk is directly proportional to
C-21
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the water concentration. Therefore, water concentra-
tions corresponding to other risk levels can be derived
by multiplying _pr dividing one of the risk levels and
corresponding water concentrations shown in the table by
factors such as 10, 100, 1,000, and so forth.
(2) Ninety-eight percent of the chlordane exposure results
from the consumption of aquatic organisms which exhibit
an average bioconcentration potential of 14,100-fold.
The remaining 2 percent of chlordane exposure results
from drinking water.
Concentration levels were derived assuming a lifetime expo-
sure to various amounts of chlordane (1) occurring from the con-
sumption of both drinking water and aquatic life grown in waters
containing the corresponding chlordane concentrations and (2)
occurring solely from consumption of aquatic life grown in the
waters containing the corresponding chlordane concentrations.
Because data indicating other sources of chlordane exposure and
their contributions to total body burden are inadequate for quan-
titative use, the figures reflect the incremental risks associated
with the indicated routes only.
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repair in cultured human cells. Mutat. Res. 42: 161.
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APPENDIX
Derivation of Criterion for Chlordane
The IRDC lifetime study of chlordane in the diet of CD-I mice
resulted in liver carcinomas in males as shown below, according to
Dr. Reuber's re-analysis of slides from the IRDC bioassay
(Epstein, 1976). Using a fish bioconcentration factor of 14,100
the water concentration estimated to result in a lifetime risk of
10~5 is calculated from the linearized multistage model using
the following parameters:
Dose Incidence
(mg/kg/day) (no. responding/no, tested)
0.0 3/33
0.65 5/55
3.25 41/52
6.5 32/39
le = 546 days w = 0.041 kg
Le = 546 days R = 14,100 I/kg
L = 546 days
With these parameters the carcinogenic potency factor for
humans, q±*, is 1.6075 (mg/kg/day)-1. The result is that
the water concentration corresponding to a lifetime risk of
10~5 is 4.6 ng/1.
U S GOVERNMENT PRINTING OFFICE 1980 720-016/4374
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