. - United States ,
Environmental Protection Office of Water EPA 811-F-95-003-T
Agency 4603 October 1995
®EPA NATIONAL PRIMARY DRINKING
WATER REGULATIONS
Contaminant Specific Fact Sheets
Synthetic Organic Chemicals - Technical Version
Adipate, (2-diethylhexyl) Ethylene Dibromide
Alachlor Glyphosate
" Aldicarb/Aldicarb Metabplites Heptachlor/Heptachlor
/ Epoxide
Atrazine Hexachlorobenzene
Benzo{a)pyrene Hexachlorocyclopentadiene
Carbofuran Lindane
Chlordane Methoxychlor
2,4-D Oxamyl (Vydate)
Dalapon Pentachlorophenol
Dibrpmochloropropane Phthalate, di(2-ethylhexyl)
Dirroseb Picloram
Dioxin^S^S-TCDD) Polychlorinated Biphenyls
Diquat Simazine
Endothall Toxaphene
Endrin 5 2,4,5 - TP (Silvex)
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United States
Environmental Protection
Agency •
Office of Water
4601
EPA 811-F-95-003a-T
October 1995
National Primary Drinking
Water Regulations
Adipate, (2-diethylhexyl)
CHEMICAL/PHYSICAL PROPERTIES
CAS NUMBER: 103-23-1
COLOR/FORM/ODOR:
Light colored, oily liquid with an
aromatic odor
M.P.: -67.8° C B.P.: 214° C
VAPOR PRESSURE: 8.5x10'7 mmHg at 25° C
OCTANOL/WATER PARTITION (Kow):
Log Kow = >6.11
DENSITY/SPEC. GRAV.: 0.922 at 25° C
SOLUBILITY: 0.78 g/L of water at 22° C;
Slightly soluble in water
SOIL SORPTION COEFFICIENT: '
Koc estimated at 5004 to 48,000;
immobile in soil
ODOR/TASTE THRESHOLDS: N/A
BlOCONCENTRATION FACTOR:
BCF = 27 in fish; not expected to
bioconcentrate in aquatic organisms.
HENRY'S LAW COEFFICIENT:
4.34x10-7 atm-cu m/mole at 20° C;
TRADE NAMES/SYNONYMS:
Adipic acid, bis(2-ethylhexyl) ester;
Bis(2-ethylhexyl) hexanedioate; BEHA;
DEHA; Adipol 2EH; Bisdflex DOA;
Dioctyl adipate; Effomoll DOA; Flexol
A26; Kodflex DOA; Monoplex DOA;
Octyl adipate; Plastomoll DOA; Sicol
250; Truflex DOA; Vestinol OA;
Wickenol 158; Witamol 320;-Ergoplast
AdDO; Kemester5652; Reomol DOA;
Rucofiex plasticizer DOA; StaflexDOA.
DRINKING WATER STANDARDS
MCLG: 0.4 mg/L
MCL: 0.4 mg/L
HAL(child): 1 day: 20 mg/L
Longer-term: 20 mg/L
HEALTH EFFECTS SUMMARY
shadow, cologne, foundations, rouge, blusher, nail-pol-
ish remover, moisturizers and indoor tanning prepara-
tions; in meat wrapping operations.
Production of adipates in 1984 was 27.5 million pounds.
RELEASE PATTERNS ,
Sources of adipates include fly ash from municipal
. . . , .-.'.. waste incineration, wastewater effluents from publicly-
..A haS n° datau°n the a°Ute toxicity of dl <2" owned treatment works (POTW) and chemical manufac-
ethylhexyl) ad.pate, or DEHA, wh.ch ,s relevant to the turj ,ants Adf ates are a|so used as a plasticizer in
drinking water context. , ,
Drinking water levels which are considered "safe" for
short-term exposures for a 10-kg (22 Ib.) child consuming
1 liter of water per day: upto a 7-year exposure to 20 mg/
L. .-•'-.-' . ..'-.-'••
Chronic: DEHA has the potential to cause the
following health effects from long-term exposures at
levels above the MCL: reduced body Weight and bone
mass; damage to liver and testes.
Cancer: There is some evidence that DEHA may have
the potential to cause cancer from a lifetime exposure at
levels above the MCL. -
USAGE PATTERNS
Adipate is used primarily as a plasticizer, commonly
blended with general purpose plasticizers in processing
polyvinyl and other polymers. It is also used as a solvent;
in aircraft lubricants; as a hydraulic fluid; as a plasticizer
or solvent in the following cosmetics: bath oils, eye
Toxic RELEASE INVENTORY -
RELEASES TO WATER AND LAND:
1987 TO 1993
Water
TOTALS (in pounds) 27,471
Top Five States*
OH 531
IN 5,500
VA 1,886
TN . 18,480
Ml 250
Major Industries*
Gray iron foundries 2,263
Aluminum foundries 250
Rubber, plastic hose/belts ,10
Space propulsion units 0
Misc Indust. organics 11,996
Land
425,230
173,900
93,275
46,102
26,409
29,750
316,438
50,409
32,078
20,363
131
* Water/Land totals only include facilities with releases
greater than a certain amount - usually 1000 to 10,000 Ibs.
October 1995
Technical Version
Printed on Recycled Paper
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PVC materials and is known to leach from plumbing
made of PVC plastic. Thus, adipates have been recog-
nized as a potential drinking water contaminant.
From 1987 to 1993, according to EPA's Toxic Chemi-
cal Release Inventory, adipate releases to land and
water totalled over 450,000 Ibs,, of which about 94
percent was to land. These releases were primarily from
gray and ductile iron foundries. The largest releases
occurred in Ohio and Indiana. The largest direct releases
to water occurred in Tennessee.
ENVIRONMENTAL FATE
If released to air, di(2-ethylhexyl) adipate (DEHA) can
exist in both vapor and particulate phases. The vapor
phase will degrade relatively rapidly by reaction with
photochemically produced hydroxyl radicals (estimated
half-life of 16 hr). The particulate phase can be physically
removed from air by wet and dry deposition.
If released to soil or water, adipate is expected to
biodegrade; activated sludge screening tests have shown
that adipate biodegrades readily, with a half-life of 2.7
days. Estimated Koc values of 5004-48,600 suggest that
adipate will be relatively immobile in soil (and not leach)
and should partition from the water column to sediment
in the aquatic environment. Volatilization is expected to
be very slow (half-life of 160 days) and not environmen-
tally important; aqueous hydrolysis is not expected to be
important except in very alkaline waters (pH 9 or higher).
Dioctyl adipate was not acutely toxic to algae and fish
at or above its water solubility of 0.78 mg/l. It was acutely
and chronically toxic to Daphnia magna at 480-850 and
24-52 ug/l, respectively. A comparison of the mean
environmental water concentration of dioctyl adipate
(<0.5 ug/L) with laboratory chronic toxicity values for
Daphnia magna showed a safety margin of approxi-
mately 3 under present use and disposal patterns, dioctyl
adipate presents a small hazard to the freshwater aquatic
environment. A whole-fish BCF of 27 was observed for
blue-gill fish was far less than an estimated BCF value in
excess of 2700 calculated from a measured log Kow of
>6.11; the difference is thought to be due to metabolism
of adipate by the bluegill. This measured BCF indicates
that bioaccumulation and persistence in fish is not impor-
tant environmentally but may be important in aquatic
organisms that are unable to metabolize adipate.
Occupational exposure can occurthrough dermal con-
tact and inhalation. The general population can be ex-
posed through consumption of foods stored in plastic
films; DEHA is used as plasticizer in various food storage
wraps and it has been shown to migrate into stored foods.
Exposure via drinking water is also possible since DEHA
is also used as a plasticizer in PVC materials and is
known to leach from plumbing made of PVC plastic.
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at >0.0006 rhg/L
ANALYSIS:
REFERENCE SOURCE . METHOD NUMBERS
EPA 600/4-88-039 506; 525^2
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
* EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
A Other sources of toxicological and environmental fate data include:
- Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
October 1995
Technical Version
Page 2
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United States
Environmental Protection
Agency
Office of Water
4601
EPA811-F-95-003b-T
•'•.'•: October 1995
National Primary Drinking
Water Regulations
Alachlor
CHEMICAL/ PHYSICAL PROPERTIES
CAS NUMBER: 15972-60-8
COLOR/ FORM/ODOR:
Available in granular, emulsifiable
concentrate and flowable formulations,
M.P.:* 40-41 °C B.P.: N/A
VAPOR PRESSURE: Negligible
DENSITY/SPEC. GRAV.: 1.133 at 25° C
OCTANOL/WATER PARTITION (Kow):
Log Kow = 2.63 and 3.53
SOLUBILITY: 0.14 g/L of water at 23° C;
.Slightly soluble in water
SOIL SORPTION COEFFICIENT: "
Koc = 2.08 to 2.28; medium to
highmobility in soil
ODOR/TASTE THRESHOLDS: N/A
BlOCONCENTRATION FACTOR:
BCF = 6 in fish; not expected to
bioconcentrate in aquatic organisms.
HENRY'S LAW COEFFICIENT:
3.2x10-8 to 1.2x10-10 atm-cu m/mole;
TRADE NAMES/SYNONYMS:
Alochlor; Lasagrin; Lassagrin; Lasso;-
Lazo; Metachlor; Pillarzo; Alanox;
Alanex; Chimichlor
DRINKING WATER STANDARDS
MCLG: zero mg/L
MCL: , 0.002 mg/L
HAL(child): 1 day: 0.1 mg/L
10-day: 0.1 mg/L
HEALTH EFFECTS SUMMARY
RELEASE PATTERNS
The major source of environmental release of alachlor
is through its manufacture and use as a herbicide.
Alachlor was detected in rural domestic well water by
EPA's National Survey of Pesticides in Drinking Water
Wells. EPA's Pesticides in Ground Water Database
reports detections of alachlor in ground water at concen-
trations above the MCL in at least 15 States.
Acute: EPA has found alachlor to potentially cause
slight skin and eye irritation from acute exposures at ENVIRONMENTAL FATE
levels above the MCL.
Drinking water levels which are considered "safe" for
short-termexposures: Fora 10-kg child consuming 1 liter
of water per day, upto a ten-day exposure to 0.1 mg/L.
Chronic: Alachlor has the potential to cause damage
to the liver, kidney, spleen, nasal mucosa and eye from
long-term exposure at levels above the MCL.
Cancer: "There is some evidence that alachlor may
have the potential to cause cancer from a lifetime expo-
sure at levels above the MCL.
USAGE PATTERNS
Alachlor is a herbicide used for preemergent control of
annual grasses, and broadleaf weeds in crops, primarily
on corn and sorghum (57%) and soybeans (43%). Appli-
cation to peanuts, cotton, vegetables and forage crops
contributes to less than 1% of its use. Alachlor is the
second most widely used herbicide in the United States,
with particularly heavy use on corn and soybeans in
Illinois, Indiana, Iowa, Minnesota, Nebraska, Ohio, and
Wisconsin.
In soil, alachlorjs transformed to its metabolites prima-
rily by biodegradation. The half-life of alachlor disappear-
ance from soil is about 15 days, although very little
mineralization has been observed. The biodegradation
of alachlor in soil-under spill conditions will be very slow
due to toxicity. Photodegradation in soil is slow.
Log Koc values for alachlor have largely been in the
range 2.08-2.28, indicating that alachlor would have a
high to medium mobility in soil, and that the leaching of
alachlor from soil is high to medium; The adsorption of
alachlor increases with an increase in organic content,
clay content and surface area of soil. Alachlor was not
detected in groundwater from a soil with high organic and
clay content. This is probably due to longer residence
time in this soil allowing the degradation of alachlor
before it reached the water table. The presence of con-
tinuous pores or channels in soil will increase the mobility
of alachlor in soil.
The evaporation of alachlor from soil will increase as
the moisture content and temperature of the soil is
increased. Increase in alachlor sorption in soil will de-
October 1995
Technical Version
Printed on Recycled Paper
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crease evaporation as evidenced by slower evaporation
with the increase in clay and organic matter content of
soil. It has been concluded that the loss of alachlor from
soil will be moderate and an estimated 3.5-6.5 kg/ha/yr or
more alachlorwill be lostfrom treated field. The estimated
half-life of alachlorevaporation from soil is in the range 12
to >200 days.
In water, both photolysis and biodegradation are im-
portant for the loss of alachlor, although the role of
photolysis becomes important in shallow clean water,
particularly in the presence of sensitizers.
The mineralization of alachlor in groundwater aquifers
was slow and <1% mineralization was observed in 30
days. The disappearance of alachlor in groundwater free
of aquifer materials (e.g., sand) was very slow and the
half-life was in the range 808-1518 days. Between alachlor
concentrations of 1-5 ppb, the disappearance rate was
faster at higher temperatures, and in groundwater taken
from shallower depths. The lower biotransformation rates
in anaerobic groundwater compared to aerobic ground-
water may be due to less microbial activity orthe absence
of alachlor degraders in anaerobic samples. The mea-
sured and estimated Henry's Law constant (H) for ala-
chlor at ambient temperatures is in the range 3.2X10-8 to
1.2X10-10 atm-cu m/m'ole, so volatilization of alachlor
from water will not be important.
The half-life of alachlor due to reaction with hydroxyl
radicals in the atmosphere has been estimated to be 2.1
hrs. Partial removal of alachlorwill also occur as a result
of dry and wet deposition.
The bioconcentration of alachlor in aquatic organisms
is not important. Whole body bioconcentration factor
(BCF) for alachlor in fathead minnow (Pimephales
promelas) was measured to be 6. Alachlor was rapidly
eliminated upon transfer offish in uncontaminated water
with 81% and 98% being eliminated after 24 hr and 14
days, respectively. The BCF value for alachlor vapor in
azalea plant leaves was experimentally determined in
greenhouse experiments to be 2.8X10+5, with elimina-
tion of alachlor from the Jeaves starting at 15 days.
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detectat>0.0002 mg'/L
METHOD NUMBERS
505; 507; 525.2; 508.1
ANALYSIS:
REFERENCE SOURCE
EPA 600/4-88-039
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
* EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
4 Other sources of toxicological and environmental fate data include:
- Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
• National Pesticide Hotline - 800/858-7378
October1995
Technical Version
Page 2
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United States Office of Water EPA 811-F-9 5-003 c-T
Environmental Protection 4601 October 199B
Agency ,
&EFA National Primary Drinking
Water Regulations
Aldicarb and Aldicarb Metabolites
CHEMICAL/ PHYSICAL PROPERTIES OCTANOL/WATER PARTITION (Kow): BiocoNCENTRATiON FACTOR:
^ Log Kow =1.13 42 in fish; not expected to bioconcen-
CAS NUMBER: 116-06-3 ^ •«„..«;,* trate in aquatic organisms. '
DENSITY/SPEC. GRAV.: 1.2at25°C .
COLOR/FORM/ODOR: -,,,,/ « . ~ HENRY'S Uw COEFFICIENT:
White crystals with slightly sulfurous SOLUBILITY: 17 ug/L of water at 25?C 1.5x10-9atm-cum/mole;
odor; Available in granular formulations e '
containing 5 to 15% aldicarb SO.L SORPT.ON COEFF.C.ENT: ^ TRADE NAMES/SYNONYMS:
^ran^shfrom8:37:hl9htovefy Temik;Carbamyl;Carbanolate;Sulfone
M.P.: 99-100° C B.P.: N/A high mobihty in soil aldoxycarb; Union Carbide 21149
VAPOR PRESSURE: IxlO^mm Hg at25° C ODOR/TASTE THRESHOLDS: N/A
DRINKING WATER STANDARDS (IN MG/L) ing crops; cotton, sugar beet, fodder beet, strawberries,
MCLG MCL HAL(CHILD) potatoes, onions, hops, vine nurseries, tree nurseries,
AWi^rh ' nnn-i n nrv* „«„« groundnuts, soya beans, citrus fruit, bananas,, coffee,
Ald,carb 0.001 0.003 none sorghum, pecans, sweet potatoes & other crops. Cotton
Aldicarb Sulfone 0.001 0.003 none crops account for 83% of aldicarb use.
Aldicarb Sulfoxide 0.001 0.004 none As the result of the aldicarb contamination of drinking
NOTE: The MCLs for aldicarb and its metabolites are water wells, Union Carbide Corporation excluded the use
presently stayed. of afdicarb products in Suffolk County, Long Island, New
.York. The company also limited the use of aldicarb
HEALTH EFFECTS SUMMARY products,to once every two years and only after plant
HEALTH EFFECTS SUMMARY emergency in the States of Maine and Wisconsin and the
Acute: EPA has found aldicarb to potentially cause Counties of Hartford in Connecticut, Kent and New Castle
nausea, diarrhea and relatively minor neurological symp- in Delaware, Franklin and Hampshire in Massachusetts,
toms resulting from acute exposures at levels above the Worchesterin Maryland, Atlantic, Burlington, Cumberland,
MCL These effects appear to be rapidly and completely Monmouth and Salem in New Jersey, Newport ahd
reversible after exposure. No Health Advisories have. Washington in Rhode Island, and Accomack and
been established for short-term exposures. Northampton in Virginia. , .
Chronic: Aldicarb has the potential to cause neuro- Aldicarb may be applied at planting at the 1 Ib active
logical effects such as sweating, pupillary constriction ingredient/acre rate for aphid control in the State of
and leg weakness from chronic exposure at levels above Maine.
the MCL. These effects are associated with the inhibition
of cholinesterase in blood and nerve tissue. RELEASE PATTERNS
C^^Therfeisinadequateevidencetostatewhet^ Release of aldicarb to the environment will occurdue
ornotertherald.carbor.tsmetabolrteshavethepotent.al to its manufacture and use as a.systemic insecticide,
to cause cancer from hfet.me exposures .in dnnkmg acarjcjde and nematocide for soil usye
water.
.. _ • ENVIRONMENTAL FATE ,
USAGE PATTERNS
,... .. ,. .. ... .,, ' , , . . „ If aldicarb is released to the soil it should not bind to the
AWICarb ,s applied to the «oil for control of chewing & soi|. |t wjl, be susceptible to cnemical and possibly bio.
sucking insects (aph.ds, wh.tefl.es, leaf m.ners, so.l- , jca| oxjdation to form jts metabolites> a|djcarb syulfox.
dwellmg msects), spiderm.tes, and nematodesJt ,s used jde and aldjcarb su,fone H dro, js js botn add and base
in glasshouse & outdoor ornamentals, and on the follow- cata|yzed with exarnpies Qyf hydyroiysis haif.|ives in soil at
October 1995 Technical Version Printed on Recycled Pap'er
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15 deg C of 9.9 days at pH 6.34 and 7.0, 23 days at pH
7.2, and 3240 days at pH 5.4. Half-lives in soil have been
reported to be 7 days in loam soil under field conditions,
a few days in green house soil; a general range of
persistence in soil of 1-15 days has been reported.
Aldicarb degraded faster in soil which had been previ-
ously treated with carbofuran.
If aldicarb is released to water it should not adsorb to
sediments or bioconcentrate in aquatic organisms. Aldi-
carb does not degrade in groundwater under aerobic
conditions unless relatively high pH (pH 8.5) exists;
reported half-lives in groundwater under anaerobic con-
ditions at pH 7.7-8.3 were 62-1300 days. Aldicarb has
been shown to be formed from aldicarb sulfoxide in
groundwater under aerobicconditions and under anaero-
bic conditions in groundwater to which glucose had been
added. Aldicarb may volatilize from soil with the rate of its
evaporation increasing with the rate of evaporation for
water.
Aldicarb may leach to the groundwater in some soils
where the rates of hydrolysis and oxidation are relatively
slow, as in the slow hydrolysis of aldicarb reported at pH's
around 5.4. It will be subject to hydrolysis which is both
acid and base catalyzed with examples of half-lives of
131 days at pH 3.95 and 6 days at pH 8.85 at 20 deg C,
and 3240 days at pH 5.5 and 15 deg C.
No information on biodegradation in natural waters
was found. It is susceptible to photolysis when irradiated
at 254 nm, but may not be photolyzed by light >290 nm.
Volatilization from water should not be an important fate
process. Half-life is 5 days in lake and pond water.
If aldicarb is released to the atmosphere it will be
subject to reaction with hydroxyl radicals with an esti-
mated vapor phase half-life of 3.49 days. No information
on photolysis at environmentally significant wavelengths
was found.
The propensity of aldicarb for bioaccumulation and
biomagnification was tested in a model ecosystem with a
terrestrial-aquatic interface and a seven-element food
chain. Aldicarb was shown to have a high degree of
persistence and a low potential for biodegradability.
A BCF of 42 for an unspecified species of fish in a
microcosm study has been reported. A BCF of 4 has
been estimated from water solubility. Based on the re-
ported and estimated BCF, aldicarb should not biocon-
centrate in aquatic organisms.
OTHER REGULATORY INFORMATION
NOTE: The MCLs for aldicarb and its metabolites
are presently stayed. Systems must monitor for
these contaminants by December 31, 1995.
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples
REPEAT FREQUENCY-none
TRIGGERS - none '
ANALYSIS:
REFERENCE SOURCE METHOD NUMBERS
EPA 600/4-88-039 531.1
Standard Methods 6610
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
* EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
4 Other sources of lexicological and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
• National Pesticide Hotline - 800/858-7378
October 1995
Technical Version
Page 2
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United States
Environmental Protection
Agency ,
Office of Water
4601
EPA 811-F-9 5-003 d-T
October 1995
National Primary Drinking
Water Regulations
Atrazine
CHEMICAL/ PHYSICAL PROPERTIES
CAS NUMBER: 1912-24-9
COLOR/ FORM/ODOR: .
Available as suspension concentrate;
wettable powder; water-dispersible
granules.
M.P.: 171-174° C , B.P.: N/A
VAPOR PRESSURE: 3x10"7 mm Hg at 20° C
DENSITY/SPEC. GRAV.: 1.19 g/mL at 20° C
OCTANOL/WATER PARTITION (Kow):
LogKow = 2.75
SOLUBILITY: 0.03 g/L of water at 20° C
ODOR/TASTE THRESHOLDS: N/A
SOIL SORPTION COEFFICIENT:
Koc average is 122; medium to high
mobility in soil
BlOCONCENTRATION FACTOR.'
Log BCF ranges from 0.3 to 2.0 in
fish; low bioconcentration potential
HENRY'S LAW COEFFICIENT:
2.63x10-9 atm-cu m/mote (calculated);
TRADE NAMES/SYNONYMS: Aatrex; Actinite PK;
Akticon; Argezin; Atazinax; Atranex;
Atrataf;,Atred; Candex; ,Cekuzina-T;
Chromozin; Crisatrina; Cyazin;
Fenamin; Fenatrol; Gesaprim; Griffex;
Hungazin; Inakor; Pitezin; Primatol;
Radazin; Strazine; Vectal; Weedex A;
Wonuk; Zeapos; Zeazine
DRINKING WATER STANDARDS
MCLG: 0.003 mg/L •
MCL: 0.003 mg/L
HAL(child): 1-to 10-day: 0.1 mg/L
Longer-term: 0.05 mg/L
HEALTH EFFECTS SUMMARY
Acute: EPA has found atrazine to potentially cause a
variety of acute health effects from acute exposures at
levels above the MCL These effects include: congestion
of heart, lungs and kidneys; hypotension; antidiuresis;
muscle spasms; weight loss; adrenal degeneration.
Drinking water levels which are considered "safe" for
short-term exposures: Fora 10-kg (22 Ib.) child consum-
ing 1 liter of water per day, a one- to ten-day exposure to
0.1 mg/L or upto a 7-year exposure to 6.05 mg/L.
Chronic: Atrazine has the potential to cause'weight
loss, cardiovascular damage, retinal and some ;muscle
degeneration, and mammary tumors from a lifetime ex-
posure at levels above the MCL.
Cancer: There js some evidence that atrazine may
have the potential to cause cancer from a lifetime expo-
sure at levels above the MCL.
USAGE PATTERNS
Atrazine is a widely used herbicide for control of
broadleaf and grassy weeds in corn, sorghum, range-
land, sugarcane, macadamia orchards, pineapple, turf
grass sod, asparagus, forestry, grasslands, grass crops,
and roses. It also was used until 1993 for control of
vegetation in fallow arid in noncrop land
Atrazine was estimated to be the most heavily used
herbicide in the United States in 1987/89, with its most
extensive use for corn and soybeans in Illinois, Indiana,
Iowa, Kansas, Missouri, Nebraska, Ohio, Texas, and
Wisconsin.
- Effective in 1993, use for non-crop vegetation control
was eliminated, and use was restricted by a requirement
for a buffer zone between application sites and surface
water. - .
RELEASE PATTERNS
Atrazine may be released to the environment through
effluents from manufacturing facilities and through its use
as a herbicide. Atrazine was the second most frequently
detected pesticide in EPA's National Survey of Pesti-
cides in Drinking Water Wells. EPA's Pesticides in
Ground Water Database indicates numerous detections
of atrazine at concentrations above the MCL in ground
water in several States, including Delaware, Illinois,
Indiana, Iowa, Kansas, Michigan, Minnesota, Missouri,
Nebraska and New York.
ENVIRONMENTAL FATE
Microbial activity possibly accounts for significant deg-
radation of atrazine in soil. The effect of atrazine on these
organisms seems to be negligible. Photodegradation
and volatilization are of little significance under most field
conditions. '
October 1995
Technical Version
Printed on Recycled Paper
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Atrazine does not hydrolyze in soils when uncatalyzed
even at elevated temperatures. However, the rate of
hydrolysis was found to drastically increase upon small
additions of sterilized soil, humic acid, and fulvic acid,
indicating atrazine hydrolysis could be catalyzed. Atr-
azine was completely hydrolyzed within 3-4 days at
extreme pHs. Alkaline hydrolysis proceeds twice as rapid
as acidic hydrolysis.
The average Koc value for 4 soils was determined to
be 122. Based on the Koc values for soils, atrazine is
expected to maintain a high to medium mobility class in
soils. However atrazine may also strongly absorb to
colloidal materials in the water column. Atrazine is more
readily adsorbed on muck or clay soils than on soils of low
clay & organic content. The downward movement or
leaching is limited by its adsorption to certain soil con-
stituents. Adsorption is not irreversible, and desprption
often occurs readily, depending on such factors as tem-
perature, moisture, and pH.
Photolysis of atrazine did not occur in water'at wave-
lengths > 300 nm. At wavelengths greater than or equal
to 290 nm, the photolysis half-life of atrazine at a concen-
tration of 10 mg/l in aqueous solution at 15 deg C was 25
hr as compared to a half-life of 4.9 hr for identical
conditions with an acetone sensitizer added at a concen-
tration of 1 ml/100 ml.
Based upon a water solubility of 30 mg/l at 20 deg C
and a vapor pressure of 2.78X10-7 mm Hg at 20 deg C, the
Henry's Law Constant for atrazine can be calculated to
be 2.63X10-5* atm-cu m/mole, which indicates volatiliza-
tion of atrazine from water will not be environmentally
important.
Reactions with photochemically produced hydroxyl
radicals in the atmosphere may be important, with reports
of an atmospheric half-life of about 2.6 hr at an atmo-
spheric concentration of 5X10+s hydroxyl radicals per cu
cm.
Experimental log BCF values of 2.0 to 0.3 have been
reported for atrazine in six fish species. Atrazine levels in
the tissues of Brook trout were below the detectable limit
after 44 weeks of exposure at a mean concentration of
0.74 mg/l. Based on these measures of BCF and uptake,
atrazine is not expected to bioconcentrate. The biocon-
centration factor predicted from water solubility = 86
(calculated); predicted from soil adsorption coefficient =
7 (calculated).
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at> 0.001 mg/L
METHOD NUMBERS
505; 507; 508.1; 525.2
ANALYSIS:
REFERENCE SOURCE
EPA 600/4-88-039
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
4 EPA can provide further regulatory and other general information:
- EPA Safe Drinking Water Hotline - 800/426-4791
4 Other sources of lexicological and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496^6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
• National Pesticide Hotline - 800/858-7378
October 1995
Technical Version
Page 2
-------
United States
Environmental Protection
Agency
Office of Water
4601
EPA811-F-95-003e-T
October 1995
National Primary Drinking
Water Regulations
Benzo(a)pyrene
CHEMICAL/ PHYSICAL PROPERTIES
CAS NUMBER: 50-32-8
COLOR/ FORM/ODOR:
Pale yellow needlelike crystals, FAINTLY
AROMATIC
M.P.: 179-179.3° C B.P.: >360°C
VAPOR PRESSURE: >1 mm Hg at 20° C
DENSITY/SPEC. GRAV.: 1.35at15°C
OCTANOL/WATER PARTITION (Kow):
Log Kow = 6.04
SOLUBILITY: 0.0038 mg/L of water at 25°
C; very low solubility in water
SOIL SORPTION COEFFICIENT:
Log Koc =6.6 to 6.8; very low mobility
in soil
' - \
ODOR/TASTE THRESHOLDS: N/A
BiocoNCENTRATioN FACTOR:
BCFs range from <1 to 2675 in fish;
expected to bioconcentrate in aquatic
organisms which are unable to metabo-
lize it. . '
HENRY'S LAW COEFFICIENT:
N/A; volatilization nonsignificant
TRADE NAMES/SYNONYMS:
3,4-Benz(a)pyrene; BaP; BP
DRINKING WATER STANDARDS
MCLG: zero rhg/L
MCL: 0.0002 mg/L
HAL(child): none
HEALTH EFFECTS SUMMARY
Acute: EPA has found polycyclic aromatic hydrocar-
bons (PAHs) similar to benzo(a)pyrene to potentially
cause the following health effects from acute exposures
at levels above the MCL: red blood cell damage, leading
to anemia; suppressed immune system.
Drinking water levels which are considered "safe" for
short-term exposures have not been established at this
time.
Chronic: Benzo(a)pyrerie has the potential to cause
the following health effects from long-term exposures at
levels above the MCL: developmental and reproductive
effects.
Cancer: There is some evidence that benzo(a)pyrene
has the potential to cause cancer from a lifetime expo-
sure at levels above the MCL.
USAGE PATTERNS
Benzo(a)pyrene is one of a group of compounds called
polycyclic aromatic hydrocarbons (PAHs), orpolynuclear
aromatic hydrocarbons (PNAs). They are not produced
or used commercially but are ubiquitous in that they are
formed as a resutt of incomplete combustion of organic
materials.
RELEASE PATTERNS
PAHs are found in exhaust from motor vehicles and
other gasoline and diesel engines, emission from coal-,
oil-, and wood-burning stoves and furnaces, cigarette
smoke; general soot and smoke of industrial, municipal,
and domestic origin, and cooked foods, especially .char-
coal-broiled; in incinerators, coke ovens, and asphalt
processing and use. ;
There are two major sources of PAHs in drinking water:
d) contamination of raw water supplies from natural and
manrmade sources, and 2) leachate from coal tar and
asphalt,linings in Water storage tanks and distribution
lines. PAHs in raw water will tend to adsorb to any
particulate matter and be removed by filtration before
reaching the tap.
PAHs ;in tap water will mainly be due to the presence
of PAH-containing materials in water storage and distri-
bution systems. Though few.data are available for esti-
mating the potential for PAH release to water from these
materials, there are reports that levels can reach 0.01 mg/
L with optimum leaching conditions. ,
ENVIRONMENTAL FATE
Released benzo(a)pyrene is largely associated with
particulate matter, soils, and sediments. Although envi-
ronmental concentrations are highest near sources, its,
presence in places djstant from primary sources indi-
cates that it is reasonably stable in the atmosphere and
capable of long distance transport. When released to air
it may be subjectto direct photolysis, although adsorption
to particulates apparently can retard this process. It may
October 1995
Technical Version
Printed on Recycled Paper
-------
also be removed by reaction with ozone (half-life 37 min)
and NO2 (half-life 7 days), and, an estimated half-life for
reaction with photochemically produced hydroxyl radi-
cals is 21.49 hr.
If released to water, it will be expected to adsorb very
strongly to sediments and particulate matter. It will not
hydrolyze. It has been shown to be susceptible to signifi-
cant metabolism by microorganisms in some natural
waters without use as carbon or energy source, but in
most waters and in sediments it is stable towards biodeg-
radation. BaP will be expected to undergo significant
photodegradation near the surface of waters. Evapora-
tion may be significant with a predicted half-life of 43
days. However, adsorption to sediments and particulates
may significantly retard biodegradation, photodegrada-
tion, and evaporation.
If released to soil it will be expected to adsorb very
strongly and will not be expected to leach to the ground-
water. However, its presence in some groundwater
samples indicates that it can be transported there by
some mechanism. It will not hydrolyze, and evaporation
from soils and surfaces is not expected to be significant.
Biodegradation tests in soils have resulted in a wide
range of reported half-lives: 2 days to 1.9 yr. Based "on
these values and the apparent lack of a significant
competing fate process, biodegradation may be an im-
portant process in soils.
Benzo(a)pyrene is expected to bioconcentrate in
aquatic organisms that can not metabolize it. Reported
BCFs include: Oysters, 3000; Rainbow trout, 920; Blue-
gills, 2,657; zooplankton, 1000 to 13,000. The presence
of humic acid in solution has been shown to decrease^
bioconcentration. Those organisms which lack a meta-'
bolic detoxification enzyme system, tend to accumulate
polycyclic aromatic hydrocarbons. For example, BCFs
have been found to be very low (<1) for mudsuckers,
sculpins and sand dabs.
Human exposure will be from inhalation of contami-
nated air and consumption of contaminated food and
water. Especially high exposure will occur through the
smoking of cigarettes and the ingestion of certain foods
(eg smoked and charcoal broiled meats and fish).
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at > 0.00002 mg/L
ANALYSIS:
REFERENCE SOURCE .. METHOD NUMBERS
EPA 600/4-88-039 525.1; 550; 550.1
>
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
* EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
A Other sources of toxicological and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
October 1995
Technical Version
Page 2
-------
United States
Environmental Protection
Agency
Office of Water
4601
EPA811-F-95-003f-T
":'. October 1995
National Primary Drinking
Water Regulations
Carbofuran
CHEMICAL/ PHYSICAL PROPERTIES
CAS NUMBER: 1563-66-2
COLOR/ FORM/ODOR: White crystalline solid
OCTANOL/WATER PARTITION (Kow):
Log Kow = 2.32
DENSITY/SPEC. GRAV.: 1.18 at 20° C
with a slightly phenolic odor. Available SOLUBILITY: 0.7 g/L of water at 25° C;
as a flowable paste or wettable
powder.
M.P.: 153-154° C B.P.: N/A
VAPOR PRESSURE:
3.4x10-6 mm Hg at 26.1° C
Slightly soluble in water
. SOIL SORPTION COEFFICIENT:
mean Koc of 29,4;
significant mobility in soil
ODOR/TASTE THRESHOLDS: N/A
BIOCONCENTRATION FACTOR:
117 in one species offish; not expected
to bioconcentrate in aquatic organisms.
HENRY'S LAW COEFFICIENT: .
1.02x10-10 atm-cu m/mole;
TRADE NAMES/SYNONYMS:
Niagara 10242, Furadan 4F or3G,
Brifur, Crisfuran, Chinufur, Curaterr,
Yaltox, Pillarfuran, Kenofuran,
DRINKING WATER STANDARDS
MCLG: 0.04 mg/L
MCL: 0.04 mg/L
HAL(child): 1 day; 0.05 mg/L
Longer-term: 0.05 mg/L
HEALTH EFFECTS SUMMARY
USAGE PATTERNS
A1984 report estimated that application on alfalfa and
rice accounted for about 90% of carbofuran use, with turf
and grapes making up most of the remainder. Earlier
uses were primarily on corn crops. This broad spectrum
insecticide is sprayed directly onto soil and plants just
after emergence to control beetles, nematodes and root-
worm.
Acute: EPA has found carbofuran to potentially cause After September 1994, carbofuran will be allowed for
a variety of nervous system effects from acute expo- use on only five U.S. crops: bananas (in Hawaii); pump-
sures, including: headache, sweating, nausea, diarrhea, kins, cucumbers, watermelons, cantaloupes and squash;
chest pains, blurred vision, anxiety and general muscular dry harvested cranberries,; pine progeny tests; and spin-
weakness. These effects.are largely due to carbofuran's ach grown for seed. Carbofuran will soon be banned from
rapid inhibition of cholinesterase activity', and is generally use on corn and sorghum in California.,;
reversible once exposure ceases. , .
i . ' • •
Drinking water levels which are considered "safe" for RELEASE PATTERNS
short-term exposures: Fora 10-kg (22 Ib.) child consum- Carbofuran enters surface water as a result of runoff
ing 1 liter of Water per day, upto a 7-year exposure to 0.05 from treated fields and enters ground water by |eaching
m9/L. of treated crops. /
Chronic: Available data on chronic toxic effects from EPA-S 1990 Natjpna| pesticide Survey djd not detect
oral exposures to carbofuran have shown that low doses carbofuran |eveis above the MCL in rural domestic wells
of carbofuran appear to have little or no adverse health or community Water System wells. EPA's Pesticides in
effects H,gher doses have the potential to cause dam- Ground Water Database reports few detections of
age to the nervous and reproductive systems. carbofuran in ground water between 1971 and 1991.
Cancer; There is na evidence that carbofuran has the
potential to cause cancer from lifetime exposures in ENVIRONMENTAL FATE
drinking water. ,
If released to soil, chemical hydrolysis and microbial
degradation appear to be the important degradation'
."'.-: processes. Chemical hydrolysis is expected to occur
more rapidly in alkaline soil as compared to neutral or
October 1995
Technical Version
Printed on Recycled Paper
-------
acidic soils. Soil biodegradation may be important, with
the rate of degradation of carbofuran in soil greatly
increased by pretreatment with carbofuran.
Experimentally measured Koc values ranging from 14
to 160 indicate that carbofuran may leach significantly in
many soils, as has been seen in the detection of carbofuran
in watertable aquifers beneath sandy soils in NY and Wl.
Leaching may not occur, however, in very high organic
content soils (65% carbon).
Volatilization from soil is not expected to be significant,
although some evaporation from plants may occur. A
review of literature reported the following half-lives for
carbofuran disappearance in soil: 2-72 days in laboratory
studies, 2-86 days for flooded soils and 26-110 days for
field soil.
If released to water, carbofuran will be subject to
significant hydrolysis under alkaline conditions. The hy-
drolysis half-lives in water at 25 deg C are 690, 8.2 and
1.0 weeks at pH 6.0, 7.0 and 8.0, respectively.
Direct photolysis and photooxidation (via hydroxyl
radicals) may contribute to carbofuran's removal from
natural water and may become increasingly important as
the acidity of the water increases and the hydrolytic half-
life increases.
Since carbofuran appears to be susceptible to degra-
dation by soil microbes, aquatic microbes may also be
able to degrade carbofuran. The half-lives for degrada-
tion of carbofuran in different waters ranges from several
hours to a few weeks.
Aquatic volatilization, adsorption, and bioconcentra-
tion are not expected to be imp.ortant.
If released to air, carbofuran will react in the vapor-
phase with photochemically produced hydroxyl radicals
at an estimated half-life of 7.8 hr. Direct photolysis may be
important removal process for carbofuran in the atmo-
sphere.
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detectat> 0.0009 mg/L
ANALYSIS:
REFERENCE SOURCE METHOD NUMBERS
EPA 600/4-88-039 531.1
Standard Methods , , 6610
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
A EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
4 Other sources of toxicologies! and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
• National Pesticide Hotline - 800/858-7378
October 1995
Technical Version
Page 2
-------
United States
Environmental Protection
Agency
Office of Water
4601
EPA811-F-95-003g-T
October "\ 995
National Primary Drinking
Water Regulations
Chlordane
CHEMICAL/PHYSICAL PROPERTIES
CAS NUMBER: 57-74-9
COLOR/FORM/ODOR:
Viscous liquid, colorless to amber, with
a slight chlorine-like aromatic odor
M.P.: 103-108° C B.P.: 175° C
VAPOR PRESSURE: 1x10-5 mm Hg at 25° C
OCTANOL/WATER PARTITION (Kow):
Log Kow = 2.78
DENSITY/SPEC. GRAV.: 1.59-1.63 at 25° C
SOLUBILITY: 0.0001 g/L of water at 25° C;
Insoluble in water
SOIL SORPTION COEFFICIENT:
log Koc estimated at 4.19 to 4.39;
very low mobility in soil
ODOR/TASTE THRESHOLDS: N/A
i "' .
HENRY'S LAW COEFFICIENT:
1.3x10-3 atm-cu m/mole (gamma-
chlordane)
BlOCONCENTRATION FACTOR: , ,
log BCF=3.6 to 4.6 in fish; significant
bioconcentration in aquatic organisms.
TRADE NAMES/SYNONYMS:
Velsicol 1068, Aspon-chlordane, Belt,
Chlorindan, Chlor-KH, Cortilan-Neu,
Dowchlor, Oktachlor, Oktaterr, Synklor,
Tat Chlor4, Topiclor, Toxichlor, Intox 8,
Gold Crest C-100, Kilex, Kypchlor,
Niran, Termi-Ded, Prentox, Pentiklor.
DRINKING WATER STANDARDS
MCLG: Zero mg/L .
MCL: 0.0(32 mg/L
HAL(child): 1 day: 0.06 mg/L
10-day: 0.06 mg/L
HEALTH EFFECTS SUMMARY
Acute: EPA has found chlordane to potentially cause
central nervous system effects - including irritability,
excess salivation, labored breathing, tremors, convul-
sions, deep depression - and blood system effects such
as anemia and certain types of leukemia.
Drinking water levels which are considered "safe" for
short-term exposures: Fora10-kg (22 Ib.) child consum-
ing 1 liter of water per day, a one- to ten-day exposure to
0.06 mg/L.
Chronic: Chlordane has the potential to damage liver,
kidneys heart lungs spleen and adrenal glands from long-
term exposure at levels above the MCL.
Cancer: There is some, evidence that chlordane may
.have the potential to cause cancer from a lifetime expo-
sure at levels above the MCL
USAGE PATTERNS
The amount of chlordane used annually in the US prior
to 1983 was estimated in 1985 to be greater that 3.6
million pounds. It was used on corn, citrus, deciduous
fruits and nuts, vegetables; for home, garden and orna-
mentals; lawns, turf, ditchbanks and roadsides. It was
applied directly to soil or foliage to control a variety of
insect pests including parasitic roundworms and other
nematodes, termites, cutworms, chiggers, leafhoppers.
After July 1,1983 the only approved use for chlordane in
the USA was for underground termite control. As of April
14,1988, however, all commercial use of chlordane in the
US has been cancelled. The only commercial use of
chlordane products still permitted is for fire ant control in
power transformers.
RELEASE PATTERNS
•••'. Chlordane has been released into the environment
primarily from its application as an insecticide.
ENVIRONMENTAL FATE
If released to soil, chlordane may persist for long
periods of time; under field conditions, the" mean degra-
dation rate has been observed to range from 4.05-
28.33%/yr with a mean half-life of 3.3 years. Chlordane is
expected to be generally immobile or only slightly mobile
in soil, however, its detection in various groundwaters in
N J and elsewhere indicates that movementto groundwa-
ter can occur. Chlordane can volatilize significantly from
soil surfaces on which it has been sprayed, particularly
moist soil surfaces; however, shallow incorporation into
soil will greatly restrict volatile losses. Although sufficient
biodegradation data are not available, it has been sug-
gested that chlordane is very slowly biotransformed in the
environment which is consistent with the long persis-
tence periods observed under field conditions.
October 1995
Technical Version
Printed on Recycled Paper
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If released to water, chlordane is not expected to
undergo significant hydrolysis, oxidation or drect pho-
tolysis. The volatilization half-life from a representative
environmental pond, river and lake are estimated to be
18-26, 3.6-5.2 and 14.4-20.6 days, respectively. How-
ever, adsorption to sediment significantly attenuates the
importance of volatilization. Biodegradation does not
seem to be an important process. Sensitized photolysis
in the water column may be possible. Adsorption to
sediment is expected to be a major fate process based on
soil adsorption data, estimated Koc values (15,500-
24,600), and extensive sediment monitoring data. The
presence of chlordane in sediment core samples sug-
gests that chlordane may be very persistent in the ad-
sorbed state in the aquatic environment.
Bioconcentration in fish is expected to be important
based on experimental BCF values which are generally
above 3,200, although there is some evidence that
accumulation is reversible over time in the absence of
further exposures. In contrast to other organochlorine
pesticides, chlordane and its degradation products do
not appear.to be extensively concentrated in the higher
members of the terrestrial food chain, ie, homeotherms.
If released to the atmosphere chlordane will be ex-
pected to exist predominately in the vapor phase. Chlor-
dane will react in the vapor-phase with photochemically
produced hydroxyl radicals at an estimated half-life rate
of 6.2 hr suggesting that this reaction is the dominant
chemical removal process. The detection of chlordane in
remote atmospheres (Pacific and Atlantic Oceans; The
Arctic) indicates that long range transport occurs.
It has been estimated that 96% of the airborne reser-
voir of chlordane exists in the sorbed state which may
explain why its long range transport is possible without
chemical transformation. The detection of chlordane in
rainwater and its observed dry deposition at various rural
locations indicates that physical removal via wet and dry
deposition occurs in the environment.
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY-, 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at > 0.0002 mg/L
METHOD NUMBERS
505; 508; 508.1; 525.2
ANALYSIS:
REFERENCE SOURCE
EPA 600/4-88-039
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
* EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
A Other sources of toxicclogical and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
• National Pesticide Hotline - 800/858-7378
October 1995
Technical Version
Page 2
-------
United States
Environmental Protection
Agency
Office of Water
4601
EPA811-F-95-003h-T
October 1995
National Primary Drinking
Water Regulations
2,4-D
CHEMICAL/PHYSICAL PROPERTIES
CAS NUMBER: 94-75-7
COLOR/ FORM/ODOR:
Colorless, odorless powder; available
as soluble liquids, powder, dust,
aerosol spray (foam)
M.P.: 138°C B.P.: 160° C
VAPOR PRESSURE: 53 Pa at 160° C
OCTANOL/WATER PARTITION (Kow):
Log Kow = 2.81
DENSITY/SPEC. GRAV.: 1.42at15°C
SOLUBILITY: 0.5 g/L of water at 20° C;
Slightly soluble in water
SOIL SORPTION COEFFICIENT:
Koc values are 19.6 to 109.1; low to
moderate mobility in soil
ODOR/TASTE THRESHOLDS: N/A
BlOCONCENTRATION FACTOR: , •
BCFs of 0.003 to 7 for various fish
and aquatic plants; not expected to
bioconcentrate in aquatic organisms.
HENRY'S LAW COEFFICIENT:
1.02x 1.0-8 atm-cu m/mole;
. TRADE NAMES/SYNONYMS: "Agent White",
Bladex-B, Brush Killer 64, Dicofur,
Dormon, Ipaner, Moxon, Netagrone,
Pielik, Verton 38, Mota Maskros,
Silvaprop 1, Agricorn D, Acme LV4,
Croprider, Fernesta, Lawn-Keep,
Penhamine D, Plantgard, Tributon,
Weed-B-Gori, Weedatul, Agroxone,
Weedar, Salvo, Green Cross Weed-No-
More 80, Red Devil Dry Weed Killer,
Scott's 4XD Weed Control, Weed-Rhap
LV40, Weedone 100, 2,4-
Dichlorophenoxyacetic acid
DRINKING WATER STANDARDS
/ ,
MCLG: 0.07 mg/L
MCL: 0.07 mg/L
HAL(child): 1 day: 1 mg/L
10-day: 0.3 mg/L
HEALTH EFFECTS SUMMARY
. Acute: EPA has found 2,4-D to potentially cause
as wheat and corn, and on pasture and rangelands.
Other uses of 2,4-D include brush control in forests, to
increase the latex output of old rubber trees, and as a
jungle defoliant. It may also be used as a plant growth
regulator to control fruit drop, such as on tomatoes to
cause all fruits to ripen at the same time for machine
harvesting.
Production of 2,4-D was steady: from 48.2 million Ibs.
;nervous system damage trom snort-term exposures at
levels above the MCL:
Drinking water levels of 2,4-D which are considered
"safe" for short-term exposures: For a 10-kg (22 Ib.) child
consuming 1 liter of water per day, a one-day exposure
of 1 mg/L, or a ten-day exposure to 0.3 mg/L
Chronic: 2,4-D has the potential to cause damage to
the nervous system, kidneys and liver from long-term
exposure at levels above the MCL.
Cancer: There is inadequate evidence to state whether
or not 2,4-D has the potential to cause cancer from
lifetime exposures in drinking water. «
USAGE PATTERNS
2,4-D is registered in the US as a herbicide for the
control of broad-leaf weeds in agriculture, and for control
of woody plants along roadsides, railways, and utilities
rights of way. It has been most widely used on such Crops
Toxic RELEASE INVENTORY -
RELEASES TO WATER AND LAND: 1987
Water
TOTALS (in pounds) 3,444
Top Five States
HI . 0
rri f
FL 5
MO 1,817
Ml 822
TX 800 ,
Major Industries
Cane sugar 0
Agri. chems. 2,616
Plastics, resins - 696
Misc. manufact. 0
Gen. Chemical 126
TO 1 993
Land
113,358 "'
73,679
38,456
0
8
0
99,886
815
0
400
8
* Water/Land totals only include facilities with releases
greater than a certain amount - usually 1000 to 10,000 Ibs. . .'•
uctooer 1995
Technical Version
Printed on Recycled Paper
-------
in 1978 to 45.1 million Ibs in 1982. 1991 data indicates
only that production exceeded 5000 Ibs. In 1991, it was
estimated that industries consumed 2,4-D as follows:
agriculture, 83 percent; for industrial/commercial uses,
11 percent; for lawns and turf, 3 percent; for aquatic uses,
3 percent.
RELEASE PATTERNS
Major environmental releases of 2,4-D are due to
agricultural applications of systemic herbicides. It is also
released as a result of the production or disposal of 2,4-
D or its by-products.
From 1987 to 1993, according to EPA's Toxic Chemi-
cal Release Inventory, 2,4-D releases to land and water
totalled over 116,000 Ibs., most of which was released to
land. These releases were primarily from cane sugar-
related industries (except refineries). The largest re-
leases (10% or more of the total) occurred in Hawaii.
especially at basic pH's. Its release to the air will also be
subject to photooxidation (estimated half-life of 1 day).
There is no evidence that bioconcentration of 2,4-D
occurs through the food chain. This has been demon-
strated by large-scale monitoring for 2,4-D residues in
soils, foods, feedstuffs, wildlife, human beings, and from
examinations of the .many routes of metabolism and
degradation that exist in ecosystems.
Human exposure will be primarily to those workers
involved in the making and using 2,4-D compounds as
herbicides as well as those who work in and live near
fields sprayed and treated with 2,4-D compounds. Expo-
sure may also occur through ingestion of contaminated
food products and drinking water.
ENVIRONMENTAL FATE
There are a variety of microorganisms in soil, freshwa-
ter and marine ecosystems which are capable of degrad-
ing 2,4-D. If released on land, 2,4-D will probably readily
biodegrade (typical half-lives <1 day to several weeks).
Reported experimental (free acid) KOC values are
19.6 to 109.1. Adsorption appears to increase with
increasing organic content and decreasing pH of soil.
Leaching to groundwater will likely be a significant pro-
cess in coarse-grained sandy soils with low organic
content or with very basic soils. In general little runoff
occurs with 2,4-D or its amine salts and runoff behavior
is the inverse of adsorption behavior. Thus, 2,4-D can be
desorbed from mineral soils, but not from those contain-
ing much organic matter.
Percolating water appears to be the principal means of
movement and diffusion is important only for transport
over very small distance. Upward movement of 2,4-D
occurs when the soil surface dries or if rapid evaporation
occurs. Thus, 2,4-D can be concentrated at the soil
surface, where it can be photolyzed, transported by wind
either on dust or in vapor form, or leached downwards
again.
If released to water, it will be lost primarily due to
biodegradation (typical half-lives 10 to >50 days). It will
be more persistent in oligotrophic waters and where high
concentrations are released. Degradation will be rapid in
sediments (half-life <1 day). Half-lives of 2-4 days were
reported for ultraviolet photolysis in water.
Volatilization of 2,4-D free acid from water and soil is
expected to be negligible based on its extremely low
reported Henry's Law constant (1.02X10-8 atm-cu m/
mole or less). It will not appreciably adsorb to sediments,
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at > '0.0005 mg/L
ANALYSIS:
REFERENCE SOURCE' ' METHOD NUMBERS
EPA 600/4-88-039 -: 515.1; 515.2; 555
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
4 EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791 .
* Other sources of toxicological and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
- National Pesticide Hotline - 800/858-7378
October 1995
Technical Version
Page 2
-------
United States
Environmental Protection
Agency
Office of Water
4601
EPA811-F-95-003J-T
October 1993
National Primary Drinking
Water Regulations
Dalapon ...'
CHEMICAL/PHYSICAL PROPERTIES DENSITY/SPEC. GRAV.: i.4ati5°c
CAS NUMBER: 75-99-0
SOLUBIUTY: 800 g/L of water at 25° C;
, . Very soluble in water
COLOR/ FORM/ODOR:
Colorless liquid with an acrid odor; sold SOIL SORPTION COEFFICIENT:
as sodium or magnesium salt Koc N/A; very high mobility in soil
ODOR/TASTE THRESHOLDS: N/A
M.P.: 20° C B.P.: 190°C
VAPOR PRESSURE: N/A
OCTANOL/WATER PARTITION (Kow):
Log Kow = 0.778 -
BlOCONCENTRATlON FACTOR:
BCF =1 to 3; not expected to biocon^
centrate in aquatic organisms.
HENRY'S LAW COEFFICIENT:
6.3x10-8 atm-cu m/mole
TRADE NAMES/SYNONYMS: 2,2-dichloro-
proprionic acid; 2,2-DPA; Revenge;
Alatex; Basfapon; Basinex; Crisapon;
Dawpon-RAE; Ded^Weed; Dowpon;
Gramevin; Kenapon; Liropon; Propon;
Radapon; Unipon; S-1315; S-95
DRINKING WATER STANDARDS
MCLG: 0.2 mg/L
MCL: 0.2 mg/L
HAL(child): 1-to 10-day: 3 mg/L
longer-term: 0.3 mg/L
of the sodium and magnesium salts.
Domestic production of dalapon in 1982 ranged be-
tween 7 and 9 million Ibs. active ingredient. In 1984, its
use in California was reported as follows: Non-food use,
92.9% (89.9% use on rights .of way); main food crop
treated was sugarbeet (6.7% of total).
HEALTH EFFECTS SUMMARY RELEASE PATTERNS
>5cute:EPAhasfounddalaPontopotentiallycausethe Dalapon is released directly to the environment in its
following health effects from acute exposures at levels use as a herbicide for thecontrol of annual and perennial
above the MCL: no effects, but readily absorbed into and grasses
widely distributed throughout the body.
Since dalapon is not a listed chemical in the Toxics
Drinking water levels which are considered "safe" for Re,ease |nventory, data on releases during its manufac-
short-term exposures: For a 10-kg (22[to.) child consum-ture and nand|j are not available.
ing 1 liter of water per day, up to a ten-day exposure to 3 .
mg/L or up to a 7-year exposure to 0.3 mg/L. - -
ENVIRONMENTAL FATE
Chronic: Dalapon has the potential to cause the
following health effects from long-term exposures at If released.*) soil, microbial degradation and leaching
levels above the MCL: increased kidney-to-body weight appear to be the important environmental fate processes,
Dalapon leaches readily in soil; however, under condi-
CancerL There is inadequate evidence to state whether tions favorable for microbialgrowth, microbial degrada-
or not dalapon has the potential to cause cancer from tion win probably proc4ed at a faster rate than leaching.
lifetime exposure in drinking water. In the absence of microbial action, dalapon degradation
in soil is slow. The resultant average persistence of
USAGE PATTERNS .* ; dalapon at recommended rates of application has been
Dalapon is a herbicide used to control grasses in aTePorted to be two to four weeks in most agricultural soils
wide variety of crops, including fruit trees, beans, coffee, durin9tne 9r°wir>g season, although a persistence of six
corn, cotton and peas. It is also registered for use in amon1:hsnasbeenobservedinsoilsofvarious forests and
number of non-crop applications such as lawns, drainagetree nursenes-
ditches, along railroad tracks, and in industrial areas. If released to water, microbial degradation, hydrolysis^
Dalapon is marketed as the sodium salt or as a mixture and photolysis are potentially important in the removal of
October 1995
Technical Version
Printed on Recycled Paper
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dalapon. The hydrolysis half-life of dalapon and its salts
in water is on the order of several months at temperatures
less than 25 deg C, with the hydrolysis forming pyruvic
acid. Under conditions favorable for microbial growth,
dalapon decomposition via microorganisms will probably
be complete within one month which will diminish the
importance of chemical hydrolysis. Direct photolysis in
water may be possible, although photolytic rates have
not been investigated under environmental conditions.
Aquatic volatilization and adsorption to sediments are not
expected to be significant.
If released to the atmosphere, dalapon will react in the
vapor-phase with photochemically produced hydroxyl
radicals at an estimated half-life rate of 72.3 days. Atmo-
spheric removal via washout may be possible since
dalapon is extremely water soluble.
Bioconcentration is not expected to be significant. The
BCF measured for dalapon (sodium salt) during a 3-day
exposure in an aquarium was 3 for fish and less than one
forsnails. BCF's of less than one have been measured for
poultry, rodents, dogs, and cows.
Occupational exposure to dalapon may occur through
dermal and inhalatiqn routes associated with the formu-
lation and application of dalapon herbicide.
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES: •
INITIAL FREQUENCY- 4 quarterly samples every 3 years
* REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons; •
1 ,sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at > 0.001 mg/L
ANALYSIS:
REFERENCE SOURCE METHOD NUMBERS
EPA 600/4-88-039 515.1; 552.1
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
/ ' *
FOR ADDITIONAL INFORMATION:
* EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
4 Other sources pf toxicological and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
• National Pesticide Hotline - 800/858-7378
October 1995
Technical Version
Page 2
-------
United States Office of Water EPA 811-F-95-003 j-T
Environmental Protection 4601 October 199B
Agency • ,
National Primary Drinking
Water Regulations
Dibromochioropropane
CHEMICAL/ PHYSICAL PROPERTIES OCTANOL/WATER PARTITION (Kow): BIOCONCENTRATION FACTOR: 11 (est.);
: ~~~ Log Kow = 2.43 (calculated) low bioconcentration potential
CAS NUMBER: 96-12-8 , , -
SOLUBILITY: 1.23g/Lofwaterat25° C; HENRY'S LAW COEFFICIENT:
COLOR/ FORM/ODOR: Slightly soluble in water I^TxIO^atm-cu m/mole;
Dense yellOw liquid with pungent odor; :
MAY ALSO BE GRANULAR SOIL SORPTION COEFFICIENT: TRADE NAMES/SYNONYMS I DBCP;
Log Koc = 2.01; high mobility BBC 12; Fumagon; Fumazone; "
M.P.: 5° C B.P.: 196° C Nemabrom; Nemafum; Nemagon;
ODOR/TASTE THRESHOLDS: Taste
VAPOR PRESSURE: 0.8 mm Hg at 21° C threshold in water is 0.01 mg/L
DENSITY/SPEC. GRAV.: 2.08 at 20° C Durham Nerriatocide EM 17,1
DRINKING WATER STANDARDS , Though it is also used as ;a chemical intermediate in the
MCLG' zero mg/L production of a flame-retardant essentially all of its
present use is as a soil fumigant. •
0.0002 mg/L
HAL(child): 1 day: 0.2 mg/L RELEASE PATTERNS : •
10-day: 0.05 mg/L In the past, release of DBCP to the environment
occurred primarily from its fumigant and nematocide
HEALTH EFFECTS SUMMARY uses. In 1977, 831, 000 pounds of DBCP was used in CA
Acute: EPA has found DBCP to potentially cause alone, mainly on grapes and tomatoes. In 1974, USA
kidney and liver damage and atrophy of the testes. farmers applied 9.8 million pounds of DBCP on crops.
Drinking water levels which are considered "safe" for All registrations of end use products were cancelled in
short-term exposures: For a 10-kg (22 Ib.) child consum- 1979 except for the use as a, soil fumigant against
ing 1 liter of water per day, a one-day exposure of 0.2 mg/nematodes on pineapples in Hawaii. This use was can-
L or a ten-day exposure to 0.05 mg/L. celled in 1985. The use of DBCP as a laboratory reactant
Chronic: DBCP has the potential to cause kidney is hot expected to result in significant release to the
damage and antifertility effects from long-term exposure environment- ,
at levels above the MCL.
CancejrvThereissomeevidencethatDBCPmayhave ENVIRONMENTAL FATE
the potential to cause cancer from a lifetime exposure at DBCP released to soij will likely volatilize or leach to
levels above the MCL. groundwater. In a model soil assumed to contain 1,2-
, dibromo-3-chloropropane (DBCP) evenly distributed
USAGE PATTERNS within the first 10cm, the volatilization half-life of DBCP
p^^_ , .'•„'• was estimated to be 1 .2 days. The observed log soil
DBCP was once used as an unclassrfied nematocide tjon C0efficient (Koc) of DBCP is 2. 11 in an unspeci-
for soil fumigation of cucumbers, summer squash, cab- fied soj| |n a soj| containing 1 Q% moisture, the log Koc of
bage, cauliflower, carrots, snap beans, okra, aster, shasta DBCp js ^ 6 Mode||ing predicted that DBCP will adsorb
daisy, ornamental turf (lawns), bermudagrass, so weaK, that jt wj,, co.migrate with water through low
centipedegrass, St Augustine grass, zoysia grass, ardisia, organjc content soil
azalea, camellia, forsythia, gardenia, hibiscus, roses,
and arborvitae. In alkaline soils, hydrolysis may be significant and
' , biodegradation is possible but is expected to be slow
October 1995 _ Technical Version : _ Printed on Recycled Paper
-------
relative to volatilization and leaching to groundwater. Soil
microorganisms (primarily Pseudomonas and
Flavobacteria) dehalogenated DBCP at a rate of 20% in
1 week at pH 8.
In water, DBCP is expected to volatilize rapidly and
hydrolyze slowly. Using measured values of the water
solubility and vapor pressure of 1230 mg/l and 0.58 mm
Hg, respectively, a Henry's Law constant of 1.47X10"4
atm-cu m/mol was estimated. The volatilization half-life
values were 9.5 hr, 13.5 hr, and 224.2 days, respectively,
for streams, rivers, and lakes.
Hydrolysis half-lives of 38 and 141 years have been
reported at 25 and 15 deg C, respectively, at pH 7. In
groundwater, DBCP is expected to persist due to its low
estimated rate of hydrolysis (half-life= 141 years at 15
deg C). Biodegradation may occur, but is expected to be
slow relative to the rate of volatilization. Sorption to
sediments and bioconcentration are not expected to be
significant fate processes.
In the atmosphere, vapor phase DBCP is expected to
react with photochemically produced hydroxyl radicals
with an estimated half-life of 12.19 days.
A bioconcentration factor for 1,2-dibromo-3-
chloropropane of 11 was estimated from a measured
water solubility of 1,230 ppm.
October 1995
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at > 0.00002 mg/L
ANALYSIS: ,
REFERENCE SOURCE METHOD NUMBERS
EPA 600/4-88-039 504.1; 551
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
* EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
* Other sources of lexicological and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
• National Pesticide Hotline - 800/858-7378
-------
United States
Environmental Protection
Agency
Office of Water
4601
EPA811-F-95-003k-T
October 1995
National Primary Drinking
Water Regulations
Dinoseb
CHEMICAL/PHYSICAL PROPERTIES
CAS NUMBER: 88-86-7
COLOR/ FORM/ODOR:
Yellow/orange crystals; pungent odor
M.P.: 38-42° C, B.P.: N/A
VAPOR PRESSURE: 1 mm Hg at 151.1° C
OCTANOL/WATER PARTITION (Kow): N/A
DENSITY/SPEC. GRAV.: 1.26 at 45° C
SOLUBILITY: 0.052 g/L of water at 25° C;
tends to form salts which are highly
soluble in water
SOIL SORPTION COEFFICIENT:
Koc =124 (measured); high mobility in
soil
ODOR/TASTE THRESHOLDS: N/A
BlOCONCENTRATION FACTOR:
BCF = 68 (est.); not expected to
bioconcentrate in aquatic organisms.
HENRY'S LAW COEFFICIENT:
5.04x1 Q-4 atm-cu m/mole (est.)
TRADE NAMES/SYNONYMS:
2,4-dinitro-6-(1-methyl-propyl) phenol;
Dinitrobutylphenol; Aatox; Chemox;
Gebutox; Knox-weed; Basanite; BNp
20; Butaphene; Dibutox; Dinitrall;
Dinitro; Desicoil; Dow Selective Weed
Killer; Hivertox; Ladob; Laseb;
Nitropone C; Dytop; Premerge; He|-fire;
Caldon; Kiloseb; Sinox General;
Subitex:
DRINKING WATER STANDARDS
MCLG: 0.007 mg/L
MCL: 0.007 mg/L -
HAL(child): 1 to 10 day: 0.3 mg/L
Longer-term: 0.01 mg/L
HEALTH EFFECTS SUMMARY
Acute: EPA has found dinoseb to potentially cause the
following health effects from acute exposures at levels
above the MCL: sweating, headache, mood changes.
Drinking water levels which are considered "safe" for
short-term exposures: Fora 10-kg (22Ib.) child consum-
ing 1 liter of water per day, a one- to ten- day exposure to
0.3 mg/L or up to a 7-year exposure to 0.01 mg/L.
Chronic: Dinoseb has the potential to cause the
following health effects from long-term exposures at
levels above the MCL: decreased body and thyroid
weight, degeneration of testes; thickening of intestinal
lining.
Cancer: There is inadequate evidence to state whether
or not dinoseb has the potential to cause cancer from
lifetime exposure in drinking water.
USAGE PATTERNS
Dinoseb is a contact herbicide used as the ammonium
or amine salt for post-emergence weed control in cereals,
undersown cereals, seedling lucerne and peas.
Oil solutions of dinoseb are used for pre-emergence
control of annual weeds in beans, peas and potatoes, for
pre-harvestdessication of hops, leguminous seed crops,
potatoes and for control of runners and suckers in straw-
berries and raspberries. ~
Dinoseb is also used as a com yield enhancer and an
insecticide and miticide.
1982 production of dinoseb was reported as 6.2 million
Ibs., with consumption estimates as follows: as an herbi-
cide for soybeans, 32%; vegetable, 23%; deciduous
fruits and nuts, 11%; peanuts, 8%; citrus, 3%; grain
crops, 2%; other field crops, 6%; industrial/commercial
uses, 15%. ,
RELEASE PATTERNS
Release of dinoseb has resulted primarily from its use
-as an herbicide on a variety of weeds.
Since dinoseb is not a, listed chemical in the Toxics
Release Inventory, data on releases during its manufac-
ture and handling are not available.
ENVIRONMENTAL FATE
Dinoseb is expected to biodegrade in slowly and bind
weakly to soil. Therefore, leaching in soil is possible and
djnoseb has been detected in groundwater. However, it
may bind more strongly to clay soils, especially at acidic
pH. Photolytic degrdration of dinoseb from soil surface
may be important. Volatilization is not expected to be
significant. The laboratory^measured evaporation half-'
October 1995
Technical Version
Printed on Recycled Paper
-------
life for dinoseb from a soil surface was 26 days. In the
absence of volatilization, the half-life of dinoseb in the
vadose zone sandy loam soil was estimated to be about
100 days.
Dinoseb may photodegrade in surface water with a
half-life of 14-18 days. The estimated Henry's Law con-
stant of 5.04X10-4 atm cu m/mol suggests that volatiliza-
tion of dinoseb from water will be slow. It is unlikely to
undergo significant biodegradation in most natural wa-
ters. Volatilization from water is expected to be slow.
The half-life for the reaction of vapor phase dinoseb
with photochemically generated hydroxyl radicals in the
atmosphere was estimated to be 14.1 days. Wet deposi-
tion may remove some of the compound from air.
Bioconcentration is expected to be insignificant. A
bioconcentration factor (BCF) of 68 for dinoseb was
estimated from its water solubility (50 mg/L).
Exposure to dinoseb in humans is expected to occur
primarily in workers using the herbicide.
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at > 0.0002 mg/L
ANALYSIS:
REFERENCE SOURCE METHOD NUMBERS
EPA 600/4-88-039 . 515.1; 515.2; 555
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
i EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
4 Other sources of toxicological and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
- National Pesticide Hotline - 800/858-7378
October 1995
Technical Version
Page 2
-------
United States
Environmental Protection
Agency
Office of Water
4601
EPA811-F-95-003I-T
October 1995
National Primary Drinking
Water Regulations
Dioxin (2,3,7,8-TCDD)
CHEMICAL/ PHYSICAL PROPERTIES
CAS NUMBER: 1746-01-6
COLOR/ FORM/ODOR:
White crystalline needles
M.P.: 305-306° C B.P.: N/A
VAPOR PRESSURE: 7.4x10r4 mm Hg, 25° C
DENSITY/SPEC. GRAY.: N/A
OCTANOL/WATER PARTITION (Kow):
LogKow = 6.8
SOLUBILITY: 19.3 ng/L of water at 25° C;
Insoluble in water
SOIL SORPTION COEFFICIENT:
Koc-N/A; very low mobility in soil
ODOR/TASTE THRESHOLDS: N/A
BlOCONCENTRATION FACTOR:
3.2 to 3.9 in fish; expected to biocon-
centrate in aquatic organisms.
HENRY'S LAW COEFFICIENT:
1:62x10"5 atm-cu m/mole;
TRADE NAMES/SYNONYMS:
2,3,7,8-Tetrachlorodibenzo-1,4-dioxin;
Dioxin; Tetradioxin;
DRINKING WATER STANDARDS
MCLG: zero mg/L
MCL: 3x10"8 mg/L
: HAL(child): 1 day: 1x10-6 mg/L
10-day: 1x10-7 mg/L .
HEALTH EFFECTS SUMMARY
Acute: EPA has found dioxin to potentially cause the
following health effects from acute exposures at levels
above the MCL: liver damage, weight loss, atrophy of
thymus gland and immunosuppression.
Drinking water levels which are considered "safe" for
short-term exposures: Fora 10-kg (22 Ib.j child consum-
ing 1 liter of water per day, a one-day exposure of 1x10-
6 mg/L or a ten-day exposure to 1 x10'7 mg/L.
Chronic: Dioxin has the potential to cause the
following health effects from long-term exposures at
levels above the MCL: variety of reproductive effects,
from reduced fertility to birth defects. ,
Cancer: There is some evidence that dioxin may have
the potential to cause cancer from a lifetime exposure at
levels above the MCL. .
USAGE PATTERNS
Dioxin is not produced or used commercially in the US.
It is a contaminant formed in the production of 2,4,5-
trichlorophenol and of a few chlprinated herbicides such
as silvex. It may also be formed during combustion of a
variety of chlorinated organic compounds.
Dioxin has been tested for use in flameproofing poly-
esters and as an insecticide, but these uses were never
exploited commercially. . ,
RELEASE PATTERNS '..-.•
2,3,7,8-TCDD is released to the environment in stack
emissions from the incineration of municipal refuse and
certain chemical wastes, in ,exhaust from automobiles
powered by leaded gasoline, in emissions from wood
burning in the presence of chlorine, in accidental fires
involving transformers containing PCBs and chlorinated
benzenes, and from the improper disposal of certain
chlorinated chemical wastes. TCDD has been released
to the environment as a low level impurity in various
pesticides (such as 2,4,5-T and derivatives) which were
manufactured from 2,4,5-trichlorophenol.
Dioxin is not a listed chemical in the Toxics Release
Inventory. Data on its incidental releases are not avail-
able. .
ENVIRONMENTAL FATE
Dioxin is one of the most toxic and environmentally
stable tricyclic aromatic compounds of its structural class.
Due to its very low water solubility, most of the 2,3,7,8-
TCDD occurring in water is expected to be associated
with sediments or suspended material. Aquatic^ sedi-
ments may be an important, and ultimate, environmental
sink for all global releases of TCDD. Two processes
which may be able to remove TCDD from water are
photolysis and volatilization.
The photolysis half-life at the water's surface has been
estimated to range from 21 hr in summer to 118 hr in
winter; however, these rates will increase significantly as
October 1995
Technical Version
Printed on Recycled Paper
-------
water depth increases. Many bottom sediments may The major route of exposure to the general population
therefore not be susceptible to significant photodegrada- results from incineration processes and exhausts from
tion. leaded gasoline engines.
The volatilization half-life from the water column of an
environmental pond has been estimated to be 46 days;
however, when the effects of adsorption to sediment are
considered, the volatilization model predicts an overall :
volatilization removal half-life of over 50 years. |
Various biological screening studies have demon-
strated that TCDD is generally resistant-to biodegrada- ,
tion. The persistence half-life of TCDD in lakes has been
estimated to be in excess of 1.5 yr.
If released to soil, TCDD is not expected to leach. As ..'...
a rule, the amount of TCDD detected more than 8 cm
below the surface has been approximately 1/10 or less
than that detected down to 8 cm. Being only slightly
soluble in water, its migration in soil may have occurred
along with soil colloids and particles to which it may have
been bound. Soil cores collected from roadsides in Times , .
Beach, MO in 1985 which had been sprayed with waste
oils containing TCDD in the early 1970s indicated that
most of the TCDD had remained in the upper 15 cm. A
mean log Koc of 7.39 was determined for ten contami-
nated soils from NJ and MO. Tests conducted by the
USDA determined that vertical movement of 2,3,7,8- ,
TCDD did not occur in a wide range of soil types.
Being only slightly soluble in water, its migration in soil
may have occurred along with soil colloids and particles
to which it may have been bound. Photodegradation on
terrestrial surfaces may be an important transformation
process. Volatilization from soil surfaces during warm
conditions may be a major removal mechanism. The
persistence half-life of TCDD on soil surfaces may vary
from less than 1 yr to 3 yrs, but half-lives in soil interiors
may be as long as 12 years. Screening studies have
shown that TCDD is generally resistant to biodegrada-
tton.
If released to the atmosphere, vapor-phase TCDD
may be degraded by reaction with hydroxyl radicals and
direct photolysis. Particulate-phase TCDD may be physi-
cally removed from air by wet and dry deposition.
Bioconcentration in aquatic organisms has been dem-
onstrated. Mean bioconcentration factors (BCF) of 29,200
(dry wt) and 5,840 (wet wt) were measured for fathead
minnows over a 28 day exposure; the elimination half-life
after exposure was found to be 14.5 days. Log BCFs of
approximately 3.2 to 3.9 were determined for rainbow
trout and fathead minnow in laboratory flow-through
studies during 4-5 exposures. The following log BCFs
have been reported forvarious aquatic organisms: snails,
fish (Gambusia), daphnia 4.3-4.4; duckweed, algae, cat-
fish, 3.6-3.95.
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS-Return to Initial ,Freq. if detect at-> 5 ng/L
METHOD NUMBERS
1613
ANALYSIS:
REFERENCE SOURCE
EPA 821-B-94-005
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
* EPA can provide further regulatory and other general infprmation:
• EPA Safe Drinking Water Hotline - 800/426-4791
4 Other sources of toxicological and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
October 1995
Technical Version
Page 2
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United States
Environmental Protection
Agency
Office of Water
4601 -
EPA811-F-95-b03mT
October 1995
National Primary Drinking
Water Regulations
Diquat
CHEMICAL/PHYSICAL PROPERTIES
CAS NUMBER: 85-00-7
COLOR/ FORM/ODOR:
Colorless to yellow crystals; water
solution is dark reddish brown
M.P.: 335-340° C B.P.: N/A
VAPOR PRESSURE: LSxIO"5 mm Hg at 20° C
OCTANOL/WATER PARTITION (Kow):
Log Kow = -3.05
DENSITY/SPEC. GRAV.: 1.22 -1.27 at 20° C
SOLUBILITY: 700 g/L of water at 20° C;
Very soluble in water
SOIL SORPTION COEFFICIENT:
Koc N/A; very low mobility in soil
ODOR/TASTE THRESHOLDS: N/A
BIOCONCENTRATION FACTOR:
Not expected to biocqncentrate in
aquatic organisms.
HENRY'S LAW COEFFICIENT:
N/A; no evaporation from water/soil
TRADE NAMES/SYNONYMS:
1,1-Ethylene 2,2-dipyridylium dibromide;
Reglone
DRINKING WATER STANDARDS
MCLG: . 0.02 mg/L
MCL: 0.02 mg/L
HAL(ehild): none
HEALTH EFFECTS SUMMARY
Acute: EPA has found diquat to potentially cause the
following health effects from acute exposures at levels
above the MCL: dehydration
Drinking water levels which are considered "safe" for
short-term exposures have, not been established
Chronic: Diquat has the potential to cause the follow-
ing health effects from long-term exposures at levels
above the MCL: cataracts.
Cancer: There is inadequate evidence to state whether
or not diquat has the potential to cause cancer from a
lifetime exposure in drinking water.
USAGE PATTERNS
Diquat is a herbicide that has been used extensively in
the US since the late 1950s to control both crop and
aquatic weeds. Its uses include potato haulm destruc-
tion; as a desiccant and defoliant to aid harvesting cotton,
rapeseed and other oil seed crops; to pre-wilt silage,
standing hay, etc. for storage; a plant growth regulator
and sugar cane-flowering suppressant.
Diquat usage in 1980wasestimatedtobe200,000lbs.
of active ingredient. 1982 data indicates that diquat was
not produced domestically, but imports were nearly
835,000 Ibs. In 1982 it was estimated that diquat usage
patterns were as follows: Industrial/commercial uses,
67%; aquatic uses, 33%.
RELEASE PATTERNS
Diquat is released into the environment during its use
as a contact herbicide, aquatjc weed control agent, seed
desiccant and sugarcane flowering suppressant agent. It
may also be released into wastewater or in spills during
its manufacture, transport and storage.
Since diquat is not a listed chemical in the Toxics
Release Inventory, data on releases during its manufac-
ture and handling are not available.
ENVIRONMENTAL FATE
Diquat is rapidly adsorbed by clay constituents of soil
and in the sorbed state is resistant to biodegradation and
photodegradation. The duration of residual activity in soil
is a few days; the deactivation resulting from its binding
to the soil. In some soils such as montprillonite clay,
adsorption is considered irreversible. There is some
evidence of a more loosely bound component, the frac-
tion of which depends on the type of soil.
Diquat is removed rapidly from aquatic systems, prin-
cipally by adsorption. If adsorption is initially to weeds,
biodegradation to soluble or volatile products occurs in
several weeks. When sorbed to sediment, little or no
degradation probably occurs. In any case, the diquat
disappears from the water in 2-4 weeks. Diquat will
photodegrade in surface layers of water in 1-3 or more
weeks when not adsorbed to particulate matter.
Should diquat be released to the atmosphere during
October 1995
Technical Version
Printed on Recycled Paper
-------
spraying operations, it would be associated with aero-
sols. It will be subject to photolysis (half-life approx 48
hrs) and gravitational settling.
Little or no bioconcentration in fish will occur, as is
expected for a chemical whose log octanol/water parti-
tion coefficient is -3.05. No residues were detected in
organs or tissues of channel catfish collected from pools
5 months after a single application or 2 months after a
second treatment of 1 ppm diquat.
Human exposure will principally be by agriculture
workers or others who use the chemical or are in the
vicinity of fields or bodies of water where diquat is used.
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to initialFreq. if detect at > 0.0004 mg/L
ANALYSIS:
REFERENCE SOURCE METHOD NUMBERS
EPA 600/4-88-039 549.1
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
* EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791,.
4 Other sources of toxicological and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
• National Pesticide Hotline - 800/858-7378
October 1995
Technical Version
Page 2
-------
United States Office of Water EPA 811-F-9,5-003 n-t
Environmental Protection 4601 October 199B
Agency ' , ' -'-•:'
National Primary Drinking
Water Regulations
Endothall
CHEMICAL/PHYSICAL PROPERTIES DENSITY/SPEC. GRAV.: 1.431 at 15° C BIOCONCENTRATION FACTOR:
~ ~~~" ro *nn „ r i "!„•,««' BCF <1 in fish; not expected to biocon-
CASNUMBER: 145-73-3 SOLUB.UTY: 100g/Lofwaterat20° C; centrate in aquatic organisms.
Very soluble in water
COLOR/FORM/ODOR: TRADE NAMES/SYNONYMS:
Odorless, white crystals SO.L SORPTONCOEFF.CIENT: Hexahydro-3,6-endo-epoxy-1,2-
NLP, 144° C (decomposes) Koc <2; h,gh mob.hty m so.l benzenedicarboxyHc acid; Accelerate;
ODOR/TASTE THRESHOLDS: N/A Aquathol; Des-i-cate; Endothall Turf
VAPOR PRESSURE: very low at room temp. Herbicide; Endothall Weed Killer;
HENRY'S LAW COEFFICIENT: N/A Herbicide 273; Hydrothol; Herbon
OCTANOL/WATER PARTITION (Kow): N/A Pennout; Hydout.
DRINKING WATER STANDARDS clover desiccants; potato vine killers.
MCLG: 0.1 mg/L , EPA estimated total domestic usage in 1982 to have
MCL: 0.1 mg/L been approximately 1.5 million Ibs. In California in 1984,
,.'...,. „..,-., no „ 87,000 Ibs. of the mono(N,N-diethylalkylamine) salt were
HAL(chHd): 1- to 10-day: 0.8 mg/L used; 4)000 |bs of the dimethylaymini sa|t w;re used;
Longer-term: 0,2 mg/L minor amounts of the dimethylalkylamine and dipotassium
salts were used. Its estimated applications in California
HEALTH EFFECTS SUMMARY were as follows: Cotton production, 95.6%; Sugarbeets,
Acute: EPA has found endothall to potentially cause 3-9%' Remainder in landscape maintenance or "public
the following health effects from acute exposures at health pest control.'"
levels above the MCL: depressed breathing and heart
rate RELEASE PATTERNS
Drinking water levels which are considered "safe" for Release of endothall to the environment is expected to
short-term exposures: For a 10-kg ,(22 Ib) child consum- pccur Pnmari|y durin9its use as a pre-emergence, post-
ing 1 liter ofwaterperday, uptp a ten-day exposure to 0.8, emergence, turf and aquatic herbicide and harvest aid.
or up to a 7-year exposure to 0 2 mg/L Other sources of release include loss during manufactur-
_. . _• ,_ „ , , ing, formulation, packaging or disposal of this herbicide.
Chronic: Endothall has the potential to cause the _.
following health effects from long-term exposures at Since endothall is not a listed chemical in the Toxics
levels above the MCL: increased organ weights and Release Inventory, data on releases during its manufac-
organ-to-body weight ratios of stomach and intestine, ture and handling are not available. x
Cancer: There is inadequate evidence to state whether ENVIRONMENTAL FATC
or not endothall has the potential to cause cancer from a ,, . . . .. . .. ,. . , . „
lifetime exposure in drinking water. ' .-. * releafed *° so"' endothall ,s expected to rap.dly
1 biodegrade under aerobic conditions. The half-life of
endothall in soil is reported to be 4 to 9 days. Endothall
USAGE PATTERNS should be highly mobile in soil; however, rapid degrada-
Endothall is used as a defoliant for a wide range of tion would limit the extent of leaching. Its persistence in
crops and as a herbicide for both terrestrial and aquatic s°il may be prolonged by adsorption to organic matter or
weeds. It is used as a desiccant on lucerne and on potato, by factors inhibiting microbial activity. Chemical hydroly-
for the defoliation of cotton, to control aquatic weeds and sis and volatilization are not expected to be significant.
as an aquatic algicidegrowthregulator.lt has been used If released to water, endothall should rapidly biode-
for: sugar beets, turf, hops sucker suppression;, alfalfa, grade under aerobic conditions (half-life approximately 1
October1995 . Technical Version Printed on Recycled Paper
-------
week or less) and biodegrade more slowly under anaero-
bic conditions. Glutamic acid is a major biotransformation
product of endothall under aerobic conditions. Endothall
is not expected to oxidize, chemically hydrolyze, photo-
lyze, volatilize or adsorb to suspended solids or sedi-
ments in water. The soil adsorption coefficient (Koc) of
endothall in sediment/water systems has been mea-
sured to be < 2.
If released to the atmosphere, endothall is expectedjto
exist predominantly on particles and should either settle
out or wash out in precipitation. It is not expected to
chemically react or photolyze in the atmosphere.
The whole body bioconcentration factor (BCF) of en-
dothall in bluegill (Lepomis macrochirus) has been mea-
sured to be < 1. Based on a its water solubility, a BCF of
< 1 has also been calculated. With these BCF values,
endothall is not expected to bioaccumulate in aquatic
organisms.
The most probable routes of human exposure to endo-
thall are inhalation and dermal contact of workers in-
volved in the manufacture, handling or application of
endothall. The general public could potentially be ex-
posed through use for lawn weed control.
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
• REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at > 0.009 mg/L
ANALYSIS:
REFERENCE SOURCE ' METHOD NUMBERS •
EPA 600/4-88-039 - 548.1
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
* EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
i Other sources of lexicological and environmentalfate data include:
• Toxic Substance Control Act Information Line - 202/554-1404 ,
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
• National Pesticide Hotline - 800/858-7378
October 1995
Technical Version
Page 2
-------
United States
Environmental Protection
Agency
Office of Water
' 4601
EPA811-F-95-0030.T
October 1995
National Primary Drinking
Water Regulations
Endrin
CHEMICAL/PHYSICAL PROPERTIES
CAS NUMBER: 72-20-8
COLOR/ FORM/ODOR:
Odorless white crystals
M.P.: 200° C B.P.: decomp. 245° C
VAPOR PRESSURE: 2x10'7 mm Hg at 25° C
OCTANOL/WATER PARTITION (Kow):
Log Kow = 5.6(calc.),
DENSITY/SPEC. GRAV.: 1.7 at 20° C
SOLUBILITY: 0.2 mg/L of water; Slightly
soluble in water
SOIL SORPTION COEFFICIENT:
Koc =34,000 (est); low mobility in soil
ODOR/TASTE THRESHOLDS: N/A
BlOCONCENTRATION FACTOR:
1335 to 10,000 in fish; expected to
bioconcentrate in aquatic organisms.
HENRY'S LAW COEFFICIENT:
4x10'7 atm-cu m/mole
TRADE NAMES/SYNONYMS:
Nendrin; EN 57; Endrex; Endricol;
Hexadrin; Mendrin; Oktanex; Com-
pound 269; Hexachloroepoxy-
octahydro-endo.endo-dimethano^-
naphthalene
DRINKING WATER STANDARDS ,
MCLG: 0.002 mg/L
MCL: 0.002 mg/L
HAL(child): 1-to 10-day: 0.02 mg/L
Longer term: 0.003 mg/L
HEALTH EFFECTS SUMMARY
Acute: EPA has found endrin to potentially cause the
following health effects from acute exposures at levels
above the MCL: tremors, labored breathing, mental con-
fusion, convulsions.
Drinking water levels which are considered "safe" for
short-term exposures: For a 10-kg (22 Ib.) child consum-
ing 1 liter of water per day, upto a ten-day exposure to
0.02 mg/L or up to a 7-year exposure to 0.003 mg/L.
Chronic: Endrin has the potential to cause the
following health effects from long-term exposures at
levels above the MCL: convulsions and damage to liver
tissue.
Cancer: There is inadequate evidence to state whether
or not endrin has the potential to cause cancer from a
lifetime exposure in drinking water.
USAGE PATTERNS .
. Endrin is an aliphatic chlorinated insecticide which has
been used mainly on field crops such as cotton, maize,
sugarcane, rice, cereals, ornamentals, and other crops.
It has also been used for grasshoppers in non-cropland
and to control voles and mice in orchards.
Once widely used in the US, most uses were cancelled
in 1980. Production in 1980 was reported to be 100,000
Ibs. - • • . :
RELEASE PATTERNS
Endrin's former source in the environment is from use
as an insect, bird and rat-killer. It has been used on
agricultural crops, cotton seeds, control of birds on build-
ings and mice in orchards. Its major use has been on
cotton crops. The U.S. EPA presently considers the,
pesticide cancelled.
ENVIRONMENTAL FATE
Endrin is very persistent, but it is known to photode-
gradeto delta-ketoendrin (half-life 7 days - June). Endrin
released to soils will persist for extremely long periods of
time (up to 14 yr or more). Biodegradation may be
enhanced somewhat in flooded soils or under anaerobic
conditions. Its low water solubility and strong adsorption
to soil makes leaching into groundwater unlikely. How-
ever, the detection of endrin in certain groundwater
samples suggest that leaching may be possible in some
soils.
Endrin's low vapor pressure suggests only limited
evaporation from soil. However, several studies have
suggested that moderate to extensive loss of endrin from
soils and crops was due to evaporation. Runoff from rain
or irrigation of particle-associated endrin will carry par^
tide-associated endrin to water systems
Endrin released to water systems will not hydrolyze or
biodegrade. It will be subject to photoisomerization to
October 1995
Technical Version
Printed on Recycled Paper
-------
ketoendrin. It will extensively sorb to sediment. Evapora-
tion from water will not be significant.
Fate of endrin in the atmosphere is unknown, but it
probably will be primarily associated with participate
matter and be removed mainly by rainout and dry depo-
sition.
There is significant bioconcentration of endrin in fish,
with BCFs of 1335-10,000 reported. In addition, there is
moderate to extensive bioconcentration in shellfish (BCF
of 500-1250) and in snails (BCF of 49,000).
Monitoring data demonstrates that endrin continues to
be a contaminant in air, water, sediment, soil, fish, and
other aquatic organisms. Human exposure appears to
come mostly from food or occupational exposure.
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES: -
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at > 0.00001 mg/L
METHOD NUMBERS
505; 508; 508.1; 525.2
ANALYSIS:
REFERENCE SOURCE
EPA 600/4-88-039
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
* EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
* Other sources of lexicological and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory; National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
• National Pesticide Hotline - 800/858-7378
October 1995
Technical Version
Page 2
-------
United States
Environmental Protection
Agency
Office of Water
4601
EPA811-F-95-003p-t
October 1995
National Primary Drinking
Water Regulations
Ethylene Dibromide
CHEMICAL/PHYSICAL PROPERTIES
CAS NUMBER: 106-93-4
COLOR/ FORM/ODOR: Colorless, heavy liquid;
mildly sweet chloroform-like odor.
M.P.: 9.8° C • B.P.: 131-132° C
VAPOR PRESSURE: 11.2 mm Hg
DENSITY/SPEC. GRAV.: 2.2 g/ml . • - -
OCTANOL/WATER PARTITION (Kow):
Log Kow =135
SOLUBILITIES: 40 g/L of water at 25° C
SOIL SORPTION COEFFICIENT (Koc):
low to moderate; Koc = 14 to 160
ODOR/TASTE THRESHOLDS: N/A
BIOCONCENTRATION FACTOR: <1 in fish
HENRY'S LAW COEFFICIENT: N/A
TRADE NAMES/SYNONYMS:
1,2-Dibromoethane; EDB; Glycol
dibromide; Bromofume; Dowfume W 85;
Aadibroom; Iscobrpme-D; Nefis;
Pestmaster; EDB-85; Soilbrdm;
Soilfume; Kopfume
DRINKING WATER STANDARDS ;
MCLG: zero mg/l
MCL: 0.00005 mg/l
HAL(child): 1 day: 0.008 mg/l
10-day: 0.008 mg/l
HEALTH EFFECTS SUMMARY
Acute: EPA has found ethylehe dibromide (EDB) to
potentially cause a variety of acute health effects, includ-
ing damage to the liver, stomach, .and adrenal cortex
along with significant reproductive system toxicity, par-
ticularly the testes. :
Drinking water levels which are considered "safe" for
short-term exposures: For a 10-kg (22 Ib.) child consum-
ing 1 liter of water per day, a one-day exposure of 0.008
mg/L or a ten-day exposure to 0.008 mg/L.
Chronic: A lifetime exposure to EDB at levels above
the MCL has the potential to damage the respiratory
system, nervous system, liver, heart, and kidneys.
Cancer: There is some evidence that EDB may have
the potential to cause cancer from a lifetime exposure at
levels above the MCL.
USAGE PATTERNS
Ethylene dibromide is mainly used (83% of all use) as
a scavenger for lead in anti-knock gasoline mixtures,
particularly in aviation fuel. Other uses (17%) include:
solvent for resins, gums, and waxes; in waterproofing
preparations; as a chemical intermediate in the synthesis
of dyes and Pharmaceuticals; and as a fumigant, insec-
ticide, nematicide for grains and fruit.
RELEASE PATTERNS
Monitoring of ethylene bromide in ocean water and
ocean air suggests that ethylene bromide may be formed
naturally in the ocean as a result of macro algae growth.
Artificial releases include: evaporative losses associ-
ated with the use, storage, and transport of leaded
gasoline in which it is used as a lead scavenger; spills and
leaking storage tanks for leaded gasoline; exhaust from
vehicles using leaded gasoline; emissions from its former
use as a fumigant for soil, grain, fruits, vegetables,
tobacco, and seed uses whicri have recently been re-
stricted or discontinued; wastewater and emissions from
its use as a solvent for resins, gums, and waxes and; as
a chemical intermediate in the synthesis of dyes and
Pharmaceuticals; residue in fumigated food.
From 1987 to 1993, according to the Toxics Release
7ox7C RELEASE INVENTORY -
RELEASES TO WATER AND LAND:
1987 TO 1993
Water
TOTALS (in pounds) 2,554
Top Six States
CA . 344
MS 342
HI 750
NJ . 0
TX 110
PR . 500
Top Industrial Sources
, Petroleum refining 2,119
Industrial organic 355
chemicals, fertilizers
Land
2,670
500
0
700
466
0
1,716
/ 700
October 1995
Technical Version
Printed on Recycled Paper
-------
Inventory EDB releases to land totalled 2,670 IDS., and
water releases totalled 2,554 Ibs. These releases were
primarily from facilities classified as petroleum refineries.
The largest of these releases occurred in California and
Missouri.
ENVIRONMENTAL FATE
When spilled on land or applied to land during soil
fumigation, ethylene dibromide will exhibit low to moder-
ate adsorption and has been found in groundwater.
Measured KOC values range from 14 to 160. However,
in typical fields where gaseous ethylene dibromide has
been used as a soil fumigant, 99% of the ethylene
dibromide used in fumigation is in the sorbed state.
Persistence can vary greatly from soil to soil. In one
laboratory screening study using 100 soils, half-lives
ranging from 1.5 to 18 weeks were determined. In one
field, ethylene bromide was detected in soil 19 years after
its last known application; the long persistence was the
result of entrapment in intraparticle micropores of the soil.
Low Koc values and detection in various ground waters
indicate that ethylene bromide will leach in soil. The
relatively high vapor pressure (11.2 mm Hg) indicates
evaporation will occur from soil surfaces.
In the atmosphere, ethylene dibromide will degrade by
reaction with photochemically produced hydroxyl radi-
cals (half life 32 days).
The primary removal process for ethylene bromide in
surface water is volatilization. Under normal conditions,
the volatilization half-life from a typical river and lake are
about one day and 5 days, respectively.
In ground waters (such as aquifers) where volatiliza-
tion does not occur, ethylene bromide can be degraded
by faiodegradation and hydrolysis. Uncatalyzed hydroly-
sis is slow, with half-lives reported of 6 yr at 25 deg C, to
13.2 yr at pH7 and 20 deg C. But hydrolysis catalyzed by
the presence of various natural substances (such as HS
ion) may be competitive with biodegradation (half-life of
1-2 months). It reacts with photochemically produced
hydroxyl radicals with a half life of 32 days or a 2.2% loss
per sunlit day. Ethylene bromide does not directly photo-
lyze when exposed to uv light between 300 and 400 nm.
Biodegradation can be a primary degradation process
in soil. A review of available biodegradation data pertain-
ing to ethylene bromide concluded that ethylene bromide
is biotransformed fairly readily in the environment; life-
times can be as short as several days in surface soils and
as long as many months in aquifer materials.
The measured log BCF in fish is < 1 indicating that
ethylene dibromide does not bioconcentrate in fish.
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
.TRIGGERS - Return to Initial Freq. if detect at > 0.00001 mg/L
ANALYSIS:
REFERENCE SOURCE METHOD NUMBERS
EPA 600/4-88-039 504.1; 551
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
4 EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
* Other sources of toxicological and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
' • Agency for Toxic Substances and Disease Registry - 404/639-6000
• National Pesticide Hotline - 800/858-7378
October 1995
Technical Version
Page.2
-------
United States .
Environmental Protection
Agency
Office of Water
4601
EPA811-F-95-003q-T
October 1995
National Primary Drinking
Water Regulations
Glyphosate
CHEMICAL/ PHYSICAL PROPERTIES DENSITY/SPEC. GRAV.: o.5g/ml at 15° C
CAS NUMBER: 1071-83-6
COLOR/ FORM/ODOR:
Odorless white crystals
M.P.:230°C B.P.: N/A
VAPOR PRESSURE: Negligible
OCTANOL/WATER PARTITION (Kow):
N/A
SOLUBILITY: 12 g/L of water at 25° C;
Soluble in water
SOIL SORPTION COEFFICIENT:
Strong, reversible adsorption
ODOR/TASTE THRESHOLDS: N/A
HENRY'S LAW COEFFICIENT: N/A
BlOCONCENTRATION FACTOR:
BCF <1 in fish; not expected to bibcon-
centrate in aquatic organisms.
TRADE NAMES/SYNONYMS:
N-(phosphonomethyl) glycine; Glialka;
Roundup; Sting; Rodeo; Spasor,-
Muster; Tumbleweed; Sonic; Glifonox;
Glycel; Rondo
DRINKING WATER STANDARDS
MCLG: 0.7 nig/L
MCL: 0.7 mg/L ,
HAL(child): 1-to 10-day: 20 mg/L
Longer-term: 1 mg/L
HEALTH EFFECTS SUMMARY
Acute: EPA has found glyphosate to potentially cause
the following health effects from acute exposures at
levels above the MCL: congestion of the lungs; increased
breathing rate.
Drinking water levels which are considered "safe" for
short-term exposures: Fora 10-kg (22 Ib.) child consum-
ing 1 liter of water per day, upto a ten-day exposure to 20
mg/L or up to a 7-year exposure to 1 mg/L.
Chronic: Glyphosate has the potential to cause the
following health effects from long-term exposures at
levels above the MCL: kidney damage,. reproductive
effects.
Cancer: There is inadequate evidence to state whether
or not glyphosate has the potential to cause cancer from
a lifetime exposure in drinking water.
beans, field com; ornamentals, lawns, turf, forest plant-
ings, greenhouses, rights-of-way.
Glyphosate is among the most widely used pesticides
by volume. In 1986, an estimated 6,308,000 pounds of
glyphosate was used in the United Sates. Usage in 1990
was estimated to be 11',595,000 pounds. It ranked elev-
enth among conventional pesticides in the US during
1990-91. In recent years, 13 to 20 million acres were
treated with 18.7 million Ibs. annually. Glyphosate is
generally sold as the isopropylamine salt and applied as
a liquid foliar spray.
RELEASE PATTERNS
Glyphosate is released to the environment in its use as
a herbicide for controlling woody and herbaceous weeds
on forestry, right-of-way, cropped and non-cropped sites.
These sites may be around water and in wetlands.
It may also be released to the environment during its
manufacture, formulation, transport, storage, disposal
and cleanup, and from spills. Since glyphosate is not a,
listed chemical in the Toxics Release Inventory, data on
releases during its manufacture and handling are not
available. ;
USAGE PATTERNS ENVIRONMENTAL FATE
Glyphosate is a non-selective herbicide registered for Glyphosate is most often applied as a spray of the
use on many food and non-food crops as well as non- isopropylamine salt and is removed from the atmosphere
crop areas where total vegetation control is desired. by gravitational settling. After glyphosate is applied to
When applied at lower rates, it serves as a plant growth forests. fields. and other land by spraying, it is strongly
regulator. The most common uses include control of adsorbed to soil, remains in the upper soil layers, and has
broadleaf weeds and grasses in : hay/pasture, soy- a low Propensity for leaching. Iron and aluminum clays
' and organic matter adsorbed more glyphosate than
Printed on Recycled Paper
October 1995
Technical Version
-------
sodium and calcium clays and was readily bound to
kaolinite, illite, bentonite, charcoal and muck but not to
ethyl cellulose.
Glyphosate readily and completely biodegrades in soil
even under low temperature conditions. Its average half-
life in soil is about 60 days. Biodegradation in foliage and
litter is somewhat faster. In field studies, residues are
often found the following year.
Glyphosate may enter aquatic systems through acci-
dental spraying, spray drift, or surface runoff. It dissipates
rapidly from the water column as a result of adsorption
and possibly biodegradation. The half-life in water is a
few days. Sediment is the primary sink for glyphosate.
After spraying, glyphosate levels in sediment rise and
then decline to low levels in a few months. Due to its ionic
state in water, glyphosate would not be expected to
volatilize from water or soil.
Based on its water solubility, glyphosate is not ex-
pected to bioconcentrate in aquatic organisms. It is
minimally retained and rapidly eliminated in fish, birds,
and mammals. The BCF of glyphosate in fish following a
10-14 day exposure period was 0.2 to 0.3.
Occupational workers and home gardeners may be
exposed to glyphosate by inhalation and dermal contact
during spraying, mixing, and cleanup. They may also be
exposed by touching soil and plants to which glyphosate
was applied. Occupational exposure may also occur
during glyphosate's manufacture, transport storage, and
disposal. ;
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at > 0.006 mg/L
ANALYSIS:
REFERENCE SOURCE METHOD NUMBERS
EPA 600/4-88-039 ' 547
Standard Methods ;• 6651
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
A EPA can provide further regulatory and other general information:
• EPA Safe Prinking Water Hotline - 800/426-4791
4 Other sources of lexicological and environmental fate data include:
- Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
• ???Nation'al Pesticide Hotline - 800/858-7378
October 1995
Technical Version
Page 2
-------
United States Office of Water EPA 811-F-95-003r-T
Environmental Protection 4601 October 1995
Agency . •
National Primary Drinking
Water Regulations
Heptachlor and Heptachlor Epoxide
CHEMICAL/PHYSICAL PROPERTIES OCTANOL/WATER PARTITION (Kow): ODOR/TASTE THRESHOLDS: N/A
CASNumber: Heptachlor-76-44-8 Log Kow = 3.9 to 5.4 (est.) B.OCONCENTRATION FACTOR:
Heptachlor epoxide-1024-57-3 DENSITY/SPEC. GRAV.: 1.57 at 9° C 5000 to 15,000 in fish; potential to
-. ,,- ,« <•.'„„„ ,, r „' „ „ bioconcentrate in aquatic organisms.
COLOR/FORM/ODOR: SOLUBILITY: 0.03 mg/Lqf water at 25 C;
White to light tan waxy solid with a insoluble in water HENRY'S LAW COEFFICIENT:
camphor-like odor. Available as „ _ „ *n. 2.62x10-3 atm-cu m/mole;
emulsifiable concentrates and oil VAPOR PRESSURE: SxlO^mm Hg at25° C
solutions. The epoxide is formed from SOIL SORPTION COEFFICIENT- TRADE NAMES/SYNONYMS:
heotachlor in the environment ^ v ^ f! I , ,0 , 3-Chlorochlordene; Aahepta;
heptachlor in the env,ronment. Lpg Koc estimated at 4,48; low to very AgrocereSj Hepta, Heptachlordane,
M.P.: 95-96° C B.P.: 145° C low mobility in soil Heptagran, Heptamul, Heptox, Gold
Crest H-60, Rhodiachlor, Velsicol 104,
Basaklor, Soleptax, Termide
DRINKING WATER STANDARDS (IN MG/L) and telephone cable boxes.
MCLG MCL HAL(1day) '•.'•':'
RELEASE PATTERNS -
Heptachlor: zero 0.0004 0.01 Heptachlor may be released directly to the soil in
-epoxide: zero 0.0002 0.01 connection with its use in termite and fire ant control.
However, heptachlorhas beenfound in treated wastewa-
HEALTH EFFECTS SUMMARY ter from some types of industrial facilities. Based on
. . ,-r,.. , • • .-. x L, ' •' ,. ., monitoring data, mean loadings in various wastestreams
. Acute EPA has found heptachlor to potentially cause are: coa| mjni . 0 0081 foundriesA 0.030 and nonfer-
hver and central nervous system damage from short- rous meta|s manufacturing. 0.Q008. .
term exposures at levels above the MCL. -
ou . . . .. .. i'•',_.,_ Heptachlor epoxide is not produced commercially, but
Short-term exposures^n dnnkmg water wh.ch are rather js fohlied by the chemjca, and bio| ica| tranysfor.
cons,dered "safe" for a 10-kg(22lb.) ch.ld consummg 1 mation of heptachlor in the environment.
liter of water per day: a one-to ten-day exposure to 0.01
mg/L- ENVIRONMENTAL FATE
Chronic: Heptachlor and its epoxide have the poten- Release of heptachlor to soil surfaces will result in
tial to cause extensive liver damage from long-term volatilization from the surface, especially in moist soils,
exposure at levels above the MCL. but volatilization of heptachlor incorporated into soil will
Cancer; There is some evidence that both heptachlor be slower. Hydrolysis in moist soils is expected to be
and heptachlor epoxide have the potential to cause significant. In soil, heptachlor will degrade to -.1-
cancer from a lifetime exposure at levels above the MGL. hydroxychlordene, heptachlor epoxide and an unidehti-
, fied metabolite less nydrpphilic than heptachlor epoxide.
USAGE PATTERNS " Biodegradation may also be significant. Heptachlor is
_ . „ ,. . ., . ._„„ , expected to adsorb strongly to soil and, therefore, to
Production of heptachlor in 1982 was nearly 100,000 resist leaching to groundwater
Ibs, all of which was used as a non-agricultural insecti- ,, .
cide. Most uses of the product were cancelled in 1978 HePtacnlor epoxide adsorbs strongly to soil and is
The only permitted commercial use of heptachlor prod- extremelyresistanttobiodegradation, persisting for many
ucts is for fire ant control in buried, pad-mounted electric years In the uPPer SO1' layers. Some volatilization or
power transformers, and in underground cable television Photo|ysis loss may occur.
\ • •• • • • '' ' • .." •..••/
October 1995 ' Technical Version • Printed on Recycled Paper
-------
Release of heptachlorto water will result in hydrolysis
to 1-hydroxychlordene (half-life of about 1 day) and
volatilization. Adsorption to sediments may occur. Bio-
degradation of heptachlor may occur, but is expected to
be slow compared to hydrolysis. Direct and photosensi-
tized photolysis may occur but are not expected to occur
at a rate comparable to that of hydrolysis. Heptachlor
epoxide will adsorb strongly to suspended and bottom
sediment when released to water. Little biodegradation is
expected.
In air, vapor phase heptachlor will react with photo-
chemically generated hydroxyl radicals with an esti-
mated half-life of 36 min. Direct photolysis may also
occur. Heptachlor epoxide is expected to exist in both the
vapor and particulate phases in ambient air. Vapor phase
reactions with photochemically produced hydroxyl radi-
cal may be an important fate process (an estimated half-
life of 1.5 days). Heptachlor epoxide that associated with
particulate matter and aerosols should be subject to
gravitational settling and washout by rain. Due to its
stability, long range dispersal occurs, resulting in the
contamination of remote areas. Some photolysis loss
probably occurs but there is no data to evaluate the rate
of this process.
Bioconcentration of heptachlor may be significant:
bioconcentration factors average around 12,000 in vari-
ous fish species. Bioconcentration may be limited, how-
ever, by the rapidity of heptachlor hydrolysis in water and
the adsorption of heptachlor to sediments. Heptachlor
epoxide is bioconcentrated extensivelyr It is taken up into
the food chain by plants and bioconcentrates into fish,
animals and milk. . • .
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if:
Heptachlor detected at > 0.0004 mg/L, or
epoxide detected at > 0.0002 mg/L
ANALYSIS:
REFERENCE SOURCE , METHOD NUMBERS
EPA 600/4-88-039 505; 508; 508.1; 525.2
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
4 EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
A Other sources of toxicological and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
• National Pesticide Hotline - 800/858-7378
October 1995
Technical Version
Page 2
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United States
Environmental Protection
Agency
Office of Water
4601
EPA811-F-95-003S-T
October
National Primary Drinking
Water Regulations
Hexachlorobenzene
CHEMICAL/PHYSICAL PROPERTIES
CAS NUMBER: 118-74-1
COLOR/ FORM/ODOR:
White needles
M.P.: 231 °C B.P.: 323-326° C
VAPOR PRESSURE: 1.09x10'5 mm Hg, 25° C
OCTANOL/WATER PARTITION (Kow):
Log Kow = 5.31 ,
DENSITY/SPEC. GRAV.: 1.57 at 23.6° C
SOLUBILITY: 0.035 mg/L of water; In-
soluble in water -
SOIL SORPTION COEFFICIENT:
Koc estimated at 4-5; low soil mobility
ODOR/TASTE THRESHOLDS: N/A _
BIOCONCENTRATION FACTOR:
Log BCF=3/1 to 4.5 in fish; expected
to bioconcentrate in aquatic organ-
isms. ,
HENRY'S LAW COEFFICIENT:
0.03 to 0.07,atm-cu m/mole; rapid
evaporation from water
TRADE NAMES/SYNONYMS:
Hexa CB, HCB, Phenyl perchloryl,
Perchlorobenzene, Pentachlorbphenyl
chloride, Anticarie, Bunt-cure,, Co-op
hexa, Julin's carbon chloride, No bunt
40, No bunt 80, Sanocide, Snieciotpx,
Smut-go, Granbx nm, Vorpnit C
DRINKING WATER STANDARDS
MCLG: zero mg/L
MCL: 0.001 mg/L
HAL(child): 1 day: 0.05 mg/L .
Longer-term: 0.05 mg/L ^
HEALTH EFFECTS SUMMARY
Acute: EPA has found hexachlbrobenzene (HGB) to
potentially cause the following health effects from acute
exposures at levels above the MCL: skin lesions, nerve
and liver damage
Drinking water levels which are considered "safe" for
short-term exposures: For a 10-kg (22 Ib.) child consum-
ing 1 liter of water per day, upto a 7-year exposure toO.05
mg/L
Chronic: HCB has the potential to cause the following
health effects from long-term exposures at levels above
the MCL: damage to liver and kidney tissue; reproductive
effects; benign tumors of endocrine glands.
Cancer: There is some evidence that HCB may have
the potential to cause cancer from a lifetime exposure at
levels above the MCL.
USAGE PATTERNS
HCB is produced as a by-product or waste material in
the production of tetrachlbroethylene, trichloroethylene,
carbon tetrachloride, chlorine, dimethyl
tetrachloroterephthalate, vinyl chloride, atrazine,
propazine, simazine, pentachloronitrobenzene, and
mirex. It is a contaminant in several pesticides including
dimethyl tetrachlorophthalate and pentachloronitroben-
zene.
Production data on hexachlorobenzene is limited. In
1982, imports were reported to be 38,000 Ibs, with no
evidence of commercial domestic production. However,
2 to 5 million Ibs may be generated each year as a waste
by-product of chlorination processes in chemical manu-
facture. . .
The greatest use of HCB is in making other organic
compounds such as rubber, dyes, wood preservatives.
Other uses of include: an additive in explosives, in
electrode manufacture, and as a fungicide on grains,
especially wheat.
RELEASE PATTERNS ,
Major environmental releases of HCB are due to air
Toxic RELEASE INVENTORY - -
RELEASES TO WATER AND LAND: 1987 TO 1993
TOTALS (in pounds)
Top States
LA
TX
Major Industries
Alkalies, chlorine
Agricultural chemicals
Water
1,286
677
609
854
297
Land
1
1
0
1
0
October 1995
Technical Version
Printed on Recycled Paper
-------
and water discharges from its production as a by-product
of chemical manufacture, or from pesticide applications.
it is also released by some waste incineration processes.
It has been detected in treated waste water, from non-
ferrous metal manufacturing.
From 1987 to 1993, according to EPA's Toxic Chemi-
cal Release Inventory, HCB releases to land and water
totalled 1,287 Ibs., all of which was to water. These
releases were primarily from alkali, chlorine and agricul-
tural chemical industries. The largest releases occurred
in Louisiana and Texas.
ENVIRONMENTAL FATE
HCB is a very persistent environmental chemical due
to its chemical stability and resistance to biodegradation.
If released to the atmosphere, HCB will exist primarily
in the vapor phase and degradation will be extremely
slow (estimated half-life with hydroxyl radicals is 2 years).
Long range global transport is possible. Physical removal
from the atmosphere can occur via washout by rainfall
and dry deposition.
If released to water, HCB will significantly partition from
the water column to sediment and suspended matter.
Volatilization from the water column is rapid (half-life of
about 8 hrs has been measured in the laboratory);
however, the strong adsorption to sediment can result in
long periods of persistence. Hydrolysis and biodegrada-
tion will not be significant processes in water.
If released to soil, HCB will be strongly adsorbed and
not generally susceptible to leaching (a half-life of 1530
days has been reported). Little biodegradation will occur
and transport to groundwater is expected to be slow,
depending upon the organic carbon content of the soil;
some evaporation from surface soil to air may occur, the
extent of which is dependent upon the organic content of
the soil.
Hexachlorobenzene-will bioconcentrate in fish and
enter into the food chain (has been detected in food
during market basket surveys). Log BCF in trout, 3.7-4.3;
sunfish, 3.1-4.3; and fathead minnow, 4.2-4.5. Similar
high BCF values (log BCF 2-3) have been measured in
aquatic microcosms.
Human exposure will be from ambient air, contami-
nated drinking water and food, as well as contact with
contaminated soil or occupational atmospheres.
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at;> 0.0001 mg/L ,
METHOD NUMBERS
505; 508; 508.1; 525.2
ANALYSIS:
REFERENCE SOURCE
EPA 600/4-88-039
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
i EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
A Other sources of toxicological and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
• National Pesticide Hotline - 800/858-7378
October 1995
Technical Version
Page 2
-------
United States
Environmental Protection
Agency
Office of Water
4601
EPA811-F-95-003t-T
October 1995
wEPA
National Primary Drinking
Water Regulations
Hexachlorocyclopentadiene
CHEMICAL/ PHYSICAL PROPERTIES
CAS NUMBER: 77-47-4
COLOR/ FORM/ODOR:
dense, oily, yellow green liquid with a
pungent odor.
M.P.: -9°C B.P.: 239° C
VAPOR PRESSURE: 0.08 mm Hg at 25° C
OCTANOL/WATER PARTITION (Kow):
Log Kow = 3.99
DENSITY/SPEC^ GRAV.: 1.7 at 25° C
SOLUBILITY: 2 m/L of water at 25° C;
Insoluble in water
SOIL SORPTION COEFFICIENT:
Koc measured at 4,265; low mobility
in soil
ODOR/TASTE THRESHOLDS: N/A ,
BlOCONCENTRATION FACTOR:
BCFs range from 100 to 1230 in fish;
some potential to bioconcentrate in
aquatic organisms.
HENRY'S LAW COEFFICIENT:
2.7x10-2 atm-cu m/mole;
TRADE NAMES/SYNONYMS:
HEX, Hexachloropentadiene
DRINKING WATER STANDARDS
MCLG: 0.05 mg/L
Met: 0.05rng/L
HAL(child): none
HEALTH EFFECTS SUMMARY
Acute: EPA has found hexachlorocyclopentadiene
(HEX) to potentially cause the following health effects
from acute exposures at levels above the MCL: gastroi-
ntestinal distress; damage to liver, kidneys and heart.
At present, EPA has issued no drinking water health
advisory providing guidance on safe levels for short-term
exposures to this chemical in drinking water.
Chronic: HEX has the potential to cause the following
health effects from long-term exposures at levels above
the MCL: damage to the stomach and kidneys.
Cancer: There is, no evidence that HEX has the
potential to cause cancer from a lifetime exposure in
drinking water.
USAGE PATTERNS
It has been estimated that between 8 and 15 million Ibs.
of HEX are produced each year.
Its greatest use is as an intermediate in chemical
manufacture, including the synthesis of chlorinated pes-
ticides, flame retardants, resins, dyes, Pharmaceuticals,
plastics, etc. HEX has ho end uses of its own.
RELEASE PATTERNS
Majorsources of release of hexachlorocyclopentadiene
to the environment are emissions and contaminated
wastewater from facilities which manufacture or use this
compound as a chemical intermediate, and from the
application of pesticides where it may remain as an
impurity. Other sources are air emissions from the incin-
eration of certain chlorinated wastes, and from water
treatment plants receiving contaminated wastestreams.
From 1987 to 1993, according to EPA's Toxic Chemi-
cal Release Inventory, HEX releases to land and water
totalled only 78 Ibs., all of which was to water. These
releases were primarily from alkalis and chlorine indus-
tries. The largest releases occurred in New York.
ENVIRONMENTAL FATE
Hexachlorocyclopentadiene is not a persistent envK
ronmental contaminant. If released to soil, it is predicted
to'be relatively immobile. In moist soil, this compound
would be subject to breakdown by light and chemical
reaction (half-life hours to weeks). Volatilization from soil
surfaces is expected to be minor.
If released to water, this compound will degrade within
minutes to hours primarily by photolysis and chemical
hydrolysis. Though^HEX can adsorb to sediments, this
does not slow its rate of degradation. Volatilization from
water is expected to be a significant removal mechanism,
although high turbidity could extend the half-life to sev-
eral weeks. Biodegradation is expected to be of minor
importance.
Hexachlorocyclopentadiene could potentially bioac-
October1995
Technical Version
Printed on Recycled Paper
-------
cumulate in some aquatic organisms depending upon
the species. Bioconcentration factors of
hexachlorocyclopentadiene in a laboratory model eco-
system: alga, 341; snail, 929; mosquito, 1634; and fish,
448.
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at > 0.0002 mg/L
METHOD NUMBERS
505; 508; 508.1; 525.2
ANALYSIS:
, REFERENCE SOURCE
EPA 600/4-88-039
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
4 EPA can provide further regulatory and other general .information:
• EPA Safe Drinking Water Hotline - 800/426-4791
4 Other sources of lexicological and environmental fate data include:
: Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
• National Pesticide Hotline - 800/858-7378
October 1995
Technical Version
. Page 2
-------
United States
Environmental Protection
Agency
Office of Water
4601 ,
EPA811-F-95-003u-T
October 1995
National Primary Drinking
Water Regulations
Lindane
CHEMICAL/ PHYSICAL PROPERTIES
CAS NUMBER: 58-89-9
COLOR/ FORM/ODOR: '
White crystalline solid
OCTANOL/WATER PARTITION (Kow):
Log Kow = 3.72 to 3:61
SOLUBILITY: 7.3 mg/L of water at 25° C;
Slightly soluble in water
SOIL SORPTION COEFFICIENT:
M.P.: 112.5°C B.P.: 323.4° C average Kbc= 1081; low soil mobility
VAPOR PRESSURE: 9.4x1 CV6 mm Hg @ 25° C ODOR/TASTE THRESHOLDS: N/A
DENSITY/SPEC. GRAV.: 1.85 ,
BiocoNCENTRAfiON FACTOR:
319 to 1613 reported in fish; some
potential to bioaccumulate.
HENRY'S LAW COEFFICIENT: N/A
TRADE NAMES/SYNONYMS:
Benzene hexachloride-gamma, gamma-
Hexachlorocyclohexane, Exagamma,
Forlin, Gallogamma, Gammaphex,
Inexit, Kwell, Lindagrandx, Lindaterra,
Lovigram, Silvanol
DRINKING WATER STANDARDS
MCLG: 0.0002 mg/L
MCL: 0.0002 mg/L
HALfchiid): 1 to 10 day: 1 mg/L
Longer term: 0.03 mg/L
HEALTH EFFECTS SUMMARY
Acute: EPA has found lindane to potentially cause
nervous system effects from short-term exposures at
levels above the MCL. High body temperature and pul-
monary edema have been reported in children with acute
exposures.
Drinking water levels which are considered "safe" for
short-term exposures: Fora 10-kg (22 Ib.) child consum-
ing 1 liter of water per day, a one- to ten-day exposure to
1 mg/L or a longer term exposure to 0.03 mg/L.
Chronic: Lindane has the potential to cause liver and
kidney damage from long-term exposure at levels above
the MCL.
Cancer: There is inadequate evidence to state whether
or not lindane has the potential to cause cancer from
lifetime exposures in drinking water.
USAGE PATTERNS
Most uses being restricted in 1983, lindane is currently
used primarily for treating wood-inhabiting beetles and
seeds. It is also used as a dip for livestock, for soil
treatment, on the foliage of fruit and nut trees, vegetables,
timber, ornamentals and for wood protection.
RELEASE PATTERNS
Lindane enters surface water as a result of runoff from
agricultural land and from home and garden applications
where it is used as an insecticide.
Data from the early 1980's reported mean loadings in
treated wastewater in kg/day as follows: coal mining -
0.0081 .foundries - 0.02 and nonferrous metals manufac-
turing - 0.0004.
From 1987 to 1993, according to EPA's Toxics Re-
lease Inventory, lindane releases to land and water
totalled 1115 Ibs.
ENVIRONMENTAL FATE
When released to water, lindane is not expected to
vojatilize significantly. The volatilization half-life of lin-
dane from water at a depth of 1 meter was estimated to
be 115 to 191 days. However, experimental volatilization,
half-life of lindane in very shallow, turbulent waters was
1.5 days. '
It is not expected to biodegrade or hydrolyze in most
surface waters. Lindane released to acidic or neutral
water is not expected to hydrolyze significantly, but in
basic water, significant hydrolysis may occur.
Transport to the sediment should be slow and result
predominantly from diffusion rather than settling. Lin-
dane may slowly biodegrade in aerobic media and will
rapidly degrade under anaerobic conditions. Lindane
has been reported to photodegrade in water in spite of the
lack of a photoreactive center, but photolysis is not
considered to be a major environmental fate process.
October 1995
Technical Version
Printed on Recycled Paper
-------
Release of lindane to soil will most likely result in
volatilization from the soil surface, but not from greater
depths. A mean Koc of 1080.9 was obtained from Koc
determinations on three soils(1). The average organic
carbon content of the soils used was 13%(1). Based on
this moderate Koc value and a water solubility of 17
ppm(2), lindane is expected to leach slowly to groundwa-
ter
Lindane in the atmosphere is likely to be subjectto rain-
out and dry deposition. The estimated half-life for the
reaction of vapor phase lindane with atmospheric hy-
droxyl radicals is 1.63 days.
Lindane will bioconcentrate slightly in fish. Bioconcen-
tration factors of 16 to 1600 are reported for a variety of
molluscs, crustaceans and fish.
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at > 0.00002 mg/L
METHOD NUMBERS
505:508:508.1:525.2
ANALYSIS:
REFERENCE SOURCE.
EPA 600/4-88-039
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
4 EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
* Other sources of toxicological and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404 ,
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
. • National Pesticide Hotline - 800/858-7378
October 1995
Technical Version
, Page 2
-------
United States
Environmental Protection
Agency
Office of Water
4601
EPA 811-F-95-003v-T
October
National Primary Drinking
Water Regulations
Methoxychlor
CHEMICAL/ PHYSICAL PROPERTIES
CAS NUMBER: 72-43-5
COLOR/ FORM/ODOR: ;
Colorjess crystals with slightly fruity
odor; available as: wettable powder;
emulsifiable, dust and aerosol concen-
trates; oil solutions
M.P.: .89 ° C B.P.: N/A
VAPOR PRESSURE: very low
DENSITY/SPEC. QRAV.: 1.41 at 25°'C
OCTANOL/WATER PARTITION (Kow):
Log Kow = 4.83,4.91 and 5.08
SOLUBILITY: 0.10 mg/L of water at 25° C;
Slightly soluble in water
HENRY'S LAW COEFFICIENT:
1.6x10'5 atm-cu m/mole at 25° C
ODOR/TASTE THRESHOLDS:
is.4.7 mg/L in water
odor threshold
SOIL SORPTION COEFFICIENT:
measured Koc ranges from 97QO to
41,000 in sand to 80,000 to 100,000
in fine silt; low mobility in soil
BlOCONCENTRAtlON FACTOR:'' .
BGFs of 1500 to 8500 in shellfish and
algae, much lower in fish; expected to
bioconcentrate in aquatic organisms.
TRADE NAMES/SYNONYMS:
2,2-bis(p-methoxyphenyI)-1,1,1- ,
trichloroethane, dianisyl trichloroethane,
Dimethoxy-DDT, Methoxy-DDT,
Chemform, Maralate, Methoxo,
' Methoxcide, Metox, Moxie •
DRINKING WATER STANDARDS ,
MCLG: 0.04 mg/L
MCL: 0.04 mg/L
HAL(child): 1 day: 0.05 mg/L
Longer-term: 0.05 mg/L
HEALTH EFFECTS SUMMARY •
Acute: EPA has found methoxychlor to potentially
cause central nervous system depression, diarrhea, and
damage to liver, kidney and heart tissue from short-term
exposures at levels above the MCL.
Drinking water levels which are considered "safe" for
short-term exposures' For a 10-kg (22 Ib.) child consum-
ing 1 liter of water per day, upto a 7-year exposure to 0.05
mg/L.
Chronic: Methoxychlor has the potential to damage
liver, kidney and heart tissue and to retard growth from
long-term exposure at levels above the MCL :'
Cancer: There is no evidence that methoxychlor has
the potential to cause cancer from lifetime exposures in
drinking water.
toxicto others. It has been used extensively in Canada for
the control of biting flies, and is also effective against
mosquitoes and houseflies.
Available information indicates production of methoxy-
chlor has decreased: from 3.7 million Ibs. in 1978 to
700,000 ibs in 1982. In 1982 it was estimated that
industries consumed methoxychlor as follows: 43 per-
cent as an insecticide for livestock and poultry, 29 per-
cent on alfalfa crops and 29 percent on citrus.
RELEASE PATTERNS
Release of methoxychlor to the environment occurs
due to its use as an insecticide for home and garden
applications, livestock and poultry, alfalfa, soya beans,
forests (Dutch Elm disease), ornamental shrubs, decidu-
ous fruits and nuts, and vegetables Other sources of
release may include loss during the manufacture, formu-
lation, packaging, and disposal of methoxychlor.
From 1987 to 1993, according to EPA's Toxic Chemi-
cal Release Inventory, methoxychlor releases to land
and water totalled only about 2000 Ibs.
ENVIRONMENTAL FATE
USAGE PATTERNS , 'Methoxychlor does" not tend to persist when released
Methoxychlor is preferred to DDT for use on animals, to soil or water' and does not accumulate in fish.
in animal feed, and on DDT-sensitive crops such as If released to soil, methoxychlor is expected to remain
squash, melons, etc. Since methoxychlor is more un- immobilized primarily in the upper layer of soil although a
stable than DDT, it has less residual effect. Compared to small percentage may migrate to lower depths, possibly
DDT, methoxychlor, is more toxic to some insects & less into groundwater as suggested by the detection of me-
Octbber 1995 . • ' • ' Technical Version . Printed on Recycled Paper
-------
thoxychlor in some groundwater samples.
Measured soil sorption coefficient (Koc) values in,
various soil are as follows: 9700 to 41,000 in sand, 80,000
to 86,000 in coarse silt, 73,000 to 100,000 in medium silt,
80,000 to 100,000 in fine silt and 73,000 to 92,000 in clay.
In another study, a Koc of 620 was found in a water-
sediment system. .
This range of Koc values suggests that methoxychlor
would be moderately mobile to immobile in soil and
adsorb significantly to suspended solids and sediments
in water. Methoxychlor was found to migrate as much as
100 cm under conditions in which 95 to 97% of the
residues remained in the top 10 cm of soil.
Under anaerobic soil/sediment conditions, biodegra-
'dation appears to be the dominant removal mechanism.
In sediments, methoxychlor was found to have a half-life
of >100 days under relatively aerobic conditions and < 28
days under anaerobic conditions. Half-lives in anaerobic
soils are about 3 months. Methoxychlor may undergo
indirect "sensitized" photolysis on the soil surfaces and
it may undergo chemical hydrolysis in moist soils (half-life
> 1 year).
If released to water, methoxychlor may be removed or
transported by several different mechanisms. Methoxy-
chlor may adsorb to suspended solids and sediments. It
may undergo direct photolysis (half-life 4.5 months) or
indirect "sensitized" photolysis (half-life <5 hours) de-
pending upon the presence of photosensitizers. Based
on the Henry's law constant, volatilization of methoxy-
chlor may be significant (half-life 4.5 days from a shallow
river).
Methoxychlor may also biodegrade in sediments, as
mentioned above, but oxidation and chemical hydrolysis
are not expected to be significant fate processes.
If released to the atmosphere, methoxychlor may exist
in either vapor or particulate form. Methoxychlor may
undergo reaction with photochemically generated hy-
droxyl radicals (estimated vapor phase half-life 3.7 hours)
or physical removal by settling out or washing out in
precipitation.
Significant bioconcentration has been measured in
certain shellfish, insects, algae and fish, although fish are
generally reported to metabolize methoxychlorfairly rap-
idly and do not accumulate it.
The most probable route of exposure to methoxychlor
would be inhalation or dermal contact during home use of
this insecticide, inhalation of airborne particulate matter
containing methoxychlor or ingestion of food or drinking
water contaminated with methoxychlor.
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
, INITIAL FREQUENCY- 4 quarterly samples every 3 years .
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at> 0.0001 mg/L
METHOD NUMBERS
505; 508; 508.1; 525.2
ANALYSIS:
REFERENCE SOURCE
EPA 600/4-88-039
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
4 EPA can provide further regulatory and other general information:
- EPA Safe Drinking Water Hotline - 800/426-4791
* Other sources of toxicological and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
• National Pesticide Hotline - 800/858-7378 ,
October 1995
Technical Version
Page 2
-------
United States
Environmental Protection
Agency
Office of Water
4601
EPA811-F-95-003wT
October 199B
National Primary Drinking
Water Regulations
Oxamyl (Vydate)
CHEMICAL/ PHYSICAL PROPERTIES
CAS NUMBER: 23135-22-0
COLOR/ FORM/ODOR:
White crystals with slight sulfurous
odor.
M.P.: 100-192° C, different .crystalline
form at 108-110° C
VAPOR PRESSURE: N/A
OCTANOL/WATER PARTITION (Kow):
DENSITY/SPEC. GRAV.: N/A
N/A
SOLUBILITY: 280 g/L of water at 25° C;
Very soluble in water
SOIL SORPTION COEFFICIENT: N/A
ODOR/TASTE THRESHOLDS: N/A
BlOCONCENTRATION FACTOR: N/A
HENRY'S LAW COEFFICIENT: N/A
TRADE NAMES/SYNONYMS:
Vydate K; Thioxamyl; Dioxamyl; DPX
1410; Dupont 1410; Methyl N'.N'-
dirhethyI-N-((methylcarbamoyl)oxy)-
1-thiooxamimidate ; *
DRINKING WATER STANDARDS
MCLG:
Met: '
0.2 mg/L
0.2 mg/L
HAL(child): 3 -to 10-day: 0.2 mg/L
Longer-term: 0.2 mg/L
HEALTH EFFECTS SUMMARY
Acute: EPA has found oxamyl to potentially cause the
following health effects from acute exposures at levels
above the MGL: tremors, salivation and tearing due to
cholinesterase inhibition.
Drinking water levels which are considered "safe" for
short-term exposures: For a 10-kg (22 Ib.) child consum-
ing 1 liter of water per day, up to a 7-year exposure to 0.2
mg/L.
Chronic: Oxamyl has the potential to cause the
following health effects from long-term exposures at
levels above the MCL: decreased body weight.
Cancer: There is no evidence that oxamyl has the
potential to cause cancer from a lifetime exposure in
drinking water.
USAGE PATTERNS
Oxamyl is widely used for control of insects, mites and
nematodes on field crops, fruits and ornamentals. The
majority of oxamyl is applied to apples (36 percent),
potatoes (33 percent), and tomatoes (20 percent).
EPA estimated that 400,000 IDS. of oxamyl were pro-
duced in the US in 1 982.
RELEASE PATTERNS
Oxamyl is released directly to the environment in its
use as an insecticide and during its manufacture, han-
dling and storage.
Since oxamyl is'not a listed chemical in the Toxics
Release Inventory, data on releases during its manufac-
ture and handling are not available.
ENVIRONMENTAL FATE
Oxamyl is highly soluble in water, and is relatively
stable in aqueous solutions at acidic pH. It hydrblyzes >
and photodegrades rapidly to an oximino compound.
Biodegradation is also rapid in soils under both aerobic
and anaerobic conditions. While laboratory studies have
found oxamyl to be mobile in soils, field data indicates
only limited mobility, most likely due to rapid biodegrada-
tion. -•
Bioconcentration is not expected as oxamyl is rapidly
absorbed, metabolized and eliminated in toxicological
tests. However, some accumulation has been noted in
the skin and hair of rodents, so accumulation may occur
in species that do not readily metabolize the compound.
Exposure data are limited, but oxamyl has been found
in drinking water at levels averaging 5 percent of the
MCL.
October 1995
Technical Version
Printed on Recycled Paper
-------
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT F:REQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at > 0.002 mg/L
ANALYSIS:
REFERENCE SOURCE METHOD NUMBERS
EPA 600/4-88-039 531.1
Standard Methods 6610
•-1 ' .
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
, I
FOR ADDITIONAL INFORMATION:
A EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
4 Other sources of lexicological and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
.-National Pesticide Hotline - 800/858-7378
October 1995
Technical Version
Page 2
-------
United States
Environmental Protection
Agency
Office of Water
4601
EPA811-F-95-003X-T
October 1995-
National Primary
Water Regulations
Pentachlorophenol
CHEMICAL/ PHYSICAL PROPERTIES
CAS NUMBER: 87-86-5
COLOR/ FORM/ODOR: White solid with
needle-like crystals and phenolic odor.
Available as: sodium salt in prills/
pellets; emulsifiable concentrate; or in
organic solvents
M.P.: 190-191 ° C B.P.: 309-310° C
VAPOR PRESSURE: 0.00011 mm Hg at 25° C
DENSITY/SPEC. GRAV.: 1.98 at 22° C
OCTANOL/WATER PARTITION:
Log Kow= 5.12
SOLUBILITY: 0.02 g/L of water at 30° C;
1 Slightly soluble in water ,
ODOR/TASTE THRESHOLDS (WATER):
Taste: 0.03 mg/L; odor: 1.6 mg/L,
SOIL SORPTION COEFFICIENT:
Koc = 3000 to 4000 in sediments; low
mobility in soil
HENRY'S LAW COEFFICIENT: N/A
BIOCONCENTRATION FACTOR:
Log BCFs of 1 to 5.7 in humans, 1 to 4
in fish; expected to bioconcentrate in
aquatic organisms.
TRADE NAMES/SYNONYMS:
PCP, Penchlorol, Dowicide 7,
Permasan, Fungifen, Grundier arbezol,
Lauxtol, Liroprem, Chlon, Dura Treet II*
Santophen 20, Woodtreat, Penta
Ready, Penta WR, Forpen-50, Ontrack
WE Herbicide, Orthq Triox, Osmose
WPC, Watershed WP, Weed and Brush
Killer
DRINKING WATER STANDARDS
MCLG: zero mg/L
"MCL: 0.001 mg/L :
HAL(chlld): 1 day: 1 mg/L
Longer-term: 0.3 mg/L
HEALTH EFFECTS SUMMARY
treating agent for beans; antibacterial agent in disinfec-
tants/cleaners; preharvesj defoliant on some crops; pre-
servative for glues, starches, photographic papers.
Production of pentachlorophenol was 45. million Ibs in
1983. In 1983 it was estimated that industries consumed
PCP as follows: Wood Preservative, 90%; Sodium
Pentachlorophenate, 10%
Acute: EPA has found pentachlorophenol to pbten- RELEASE PATTERNS
tially cause central nervous system effects from short-
term exposures at levels above the MCL.
Drinking water levels which are considered "safe" for
short-term exposures: For a 10-kg (22 Ib.) child consum-
ing 1 liter of water per day, ah exposure to 1 mg/L for one
day or an exposure to 0.3 mg/L for up to 7 years.
Chronic: Pentachlorophenol has the potential to
cause reproductive effects and damage to liver and
kidneys from long-term exposure at levels above the
MCL
Cancer: There is some evidence that pentachlorophe-
nol may have the potential to cause cancer from a lifetime
exposure at levels above the MCL. ,
USAGE PATTERNS
The greatest uses of pentachlorophenol are as a wood
preservative (fungicide). Though once widely used as an
herbicide, was banned in 1987 for these and other uses,
as well as for any over-the-counter sales.
Other uses included: soil fumigant for termites; seed
Pentachlorophenol may be released to the environ-
ment as a result of its manufacture, storage, transport, or
use as an industrial wood preservative for utility pojes,
Toxic RELEASE INVENTORY -
RELEASES TO WATER AND LAND:
1987 TO 1993
TOTALS (in pounds)
Top Five States
NV
OR
WA .
AR
GA
Major Industries
Explosives
Wood preserving
Misc. Chemicals
Water
18,700
0
4,313
3,310
2,735
783
0
17,720 \
250 •
Land
79,780
64,100
5,405
5,995
1,615
1,255
34,100
15,678
30,000
* Water/Land totals only include facilities with releases
greater than a certain amount - usually 1000 to 10,000 Ibs.
October 1995
Technical Version
Printed on Recycled Paper
-------
cross arms, and fenceposts, and other items that con-
sumes about 90% of its production.
Other former uses that may have lead to its 'release
were the manufacture of sodium pentachlorophenolate
and minor uses as a fungicide, bactericide, algicide, and
herbicide for crops, leathers and textiles.
Pentachlorophenol's used on wood is "restricted" and its
non-wood use is undergoing special review by EPA.
From 1987 to 1993, according to EPA's Toxic Chemi-
cal Release Inventory, pentachlorophenol releases to
land and water totalled nearly 100,000 Ibs., of which
about 80 percent was to land. The most widespread
releases were primarily from wood preserving industries
in many states. However, the great majority of releases
occurred at a military munitions plant in Nevada.
ENVIRONMENTAL FATE
Releases to soil can decrease in concentrations due to
slowbiodegradation and leaching into groundwater. Pen-
tachlorophenol has a tendency to adsorb to soil and
sediment; calculated Koc= 1000, measured sediment
Koc= 3,000-4,000. Adsorption to oxidized sediment is
higher than to reduced sediment. Adsorption to soil and
sediment appears to be pH dependent, stronger under
acid conditions. The Koc values for the total dissociated
phenol was calculated to be 1250 and 1800 for light and
heavy loam, respectively, while for the undissociated
species, the Koc is 25,000.
Pentachlorophenol does biodegrade but may require
several weeks for acclimation. Half-life in soil is approxi-
mately weeks to months. In an artificial stream, microbial
degradation became significant after 3 weeks and ac-
counted for 26-46% removal. Pentachlorophenol miner-
alization in water from several sites was very low (<5 ng/
L per day). 3 and 5 ppm PCP were completely degraded
in 38 and 57 days respectively when incubated in unsat-
urated soils taken at 4 and 4.5 m depths.
If released in water, pentachlorophenol will adsorb to
sediment, photodegrade (especially at higher pHs) and
slowly biodegrade. The low water solubility and moder-
ate vapor pressure would suggest that evaporation from
water is not rapid, especially at natural pHs where pen-
tachlorophenol is present in the dissociated form (pKa=
4.74). Biodegradation in the streams, or in specific stream
compartments such as the sediment or water column,
was characterized by an adaptation period (3-5 weeks for
the stream as a whole, and reproducible from the previ-
ous year), which was inversely dependent on the con-
centration of pentachlorophenol and microbial biomass.
, Pentachlorophenol does not appear to oxidize or hy-
drolyze under environmental conditions; however, pho-
tolysis of the dissociated form in water appears to be a
significant process. A measured photolysis half-life has
been reported to be 0.86 hrs.
In air, pentachlorophenol will be lost due to photolysis
and reaction with photochemically produced hydroxyl
radicals.
Bioconcentration in fish will be moderate. Pentachloro-
phenol is expected to bioconcentrate because of its low
water solubility, but the bioconcentration factor will be
dependent upon the pH of the water since pentachloro-
phenol will be more dissociated at higher pHs.
The log BCF with goldfish varied from 0.30 at pH 10 to
1.75 at pH 7 to 2.12 at pH 5.5. Other reported log BCF
values are 2.89 in fathead minnow; 2.4-3.73 in rainbow
trout; 0.7-1.7 in sheepshead minnows; and 2.47 in mos-
quito fish; 2.85 in zebra fish; 2.62 in golden brfe. The
accumulation increased with temperature in orfe and
decreased with temperature in zebra fish. The BCF of
PCP in humans was measured from daily intake of PCP
and measured concentration in different tissues, giving
the following results: 5.7, 3.3, 1.4, 1.4, and 1.0 in liver,
brain blood, spleen and adipose tissue respectively.
Humans will be occupationally exposed to pentachlo-
rophenol via inhalation and dermal contact primarily in
situations where they use this preservative or are in
contact with treated wood product. The general popula-
tion will be exposed primarily from ingesting food con-
taminated with pentachlorophenol.
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- ' 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at > 0.00004 mg/L
METHOD NUMBERS
515.1; 515.2; 525.2; 555
ANALYSIS:
REFERENCE SOURCE
EPA 600/4-88-039
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
4 EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426^791
* Other sources of lexicological and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
• National Pesticide Hotline - 800/858-7378
October 1995
Technical yersion
Page 2
-------
United States
Environmental Protection
Agency
Office of Water
4601
EPA811-F-95-OQ3y-T
October 1995
National Primary Drinking
Water Regulations
Phthalate, di(2-ethylhexyl)
CHEMICAL/ PHYSICAL PROPERTIES
CAS NUMBER: 117-81-7
COLOR/ FORM/ODOR:
Colorless oily liquid
SOLUBILITY: 0.285 mg/L of water at 24° C;
Slightly soluble in water
SOIL SORPTION COEFFICIENT:
Log Koc measured at 4 to 5; low
mobility in soil
M.P.: -50° C B.P.: 230° C (5 mm Hg) ODOR/TASTE THRESHOLDS: N/A
VAPOR PRESSURE: 1.32 mm Hg at 200° C BIOCONCENTRATION FACTOR:
Log BCF =2 to 4 in fish; expected to
bioconcentrate in aquatic organisms.
OCTANOtJWATER' PARTITION (Kow):
.Log Kow = 4.89
TRADE NAMES/SYNONYMS:
DEHP; Bis(2-ethylhexyl)-phthalate;
-BEHP; Dioctyl phthalate; Pittsburgh PX-
138; Platinol AH; RC Plasticizer OOP;
Reomol D79P; Sicol 150; Staflex OOP;
Truflex OOP; Vestinol AH; Vinicizer 80;
Palatinol AH; Hercoflex 260; Kodaflex
OOP; Mollan O; Nuoplaz OOP; Octoil;
Eviplast 80; Fleximel; Flexpl OOP;
Good-rite GP264; Hatcof OOP;
Ergoplast FDO; DAF 68; Bisoflex.81
DENSITY/SPEC. GRAV.: 0.99 at 20° C
HENRY'S LAW COEFFICIENT:
1x10-4 atm-cu m/mole
DRINKING WATER STANDARDS
MCLG: zero
MCL: 0.006 mg/L
HAL(child): none
HEALTH EFFECTS SUMMARY
Acute: EPA has found di (2-ethylhexyl) phthalate
(DEHP) to potentially cause the following health effects
from acute exposures at levels above the MCL: mild
gastrointestinal disturbances, nausea, vertigo.
Chronic: DEHP has the potential to cause the
following health effects from long-term exposures at
levels above the MCL: damage to liver and testes;
reproductive effects.
Cancer: There is some evidence that DEHP may have
the potential to cause cancer from a lifetime exposure at
levels, above the MCL.
USAGE PATTERNS
DEHP is the most commonly used of a group of related
chemicals called phthalates or phthalic acid esters.The
greatest use of DEHP is as a plasticizer for
polyvinylchloride (PVC) and other polymers including
rubber, cellulose and styrene. A number of packaging
materials and tubings used in the production of foods and
beverages are polyvinyl chloride contaminated with
phthalic acid esters, primarily DEHP.
It is also used widely in insect repellant formulations
cosmetics, rubbing alcohol, liquid soap, detergents, deco-
rative inks, lacquers, munitions, industrial and lubricating
oils, defoaming agents during paper and paperboard
manufactures, and as pesticide carriers, in photographic
film, wire and cable, adhesives, as an organic vacuum
pump fluid, a dielectric in capacitators.
Production of DEHP increased during the 1980s, from
251 million Ibs in 1982 to over286 million Ibs. in 1986, with
imports of 6 million Ibs. In 1986, it was estimated that
industries' consumed DEHP as follows: plasticizer for
polyvinyl chloride, 95%; other uses, 5%.
Toxic RELEASE INVENTORY T
RELEASES TO WATER AND LAND: 1987 TO 1993
Water
TOTALS* (in pounds) 16,910
Top Five States*
Wl . • ' 500
TN 3,491
OH 268
NJ 3,956
NY 500
Major Industries
Misc rubber products , 274
Rubber, plastic hose 10
Cyclic crudes, intermed. 3,099
Land
471,191
255,000
80,419
62,982
23,139
13,284
311,900
80,019
12;200
* Water/Land totals only include facilities with releases
greater than 100 Ibs.
October 1995
Technical Version
Printed on Recycled Paper
-------
RELEASE PATTERNS
DEHP is used in large quantities, primarily as a plasti-
cizerfor polyvinyl chloride and other polymeric materials.
Disposal of these products (incineration, landfill, etc) will
resultinthe release of DEHPinto the environment. DEHF*
has been detected in the effluent of numerous industrial
plants.
From 1987 to 1993, according to EPA's Toxic Chemi-
cal Release Inventory, DEHP releases to land and water
totalled over 500,000 IDS., of which about 95 percent was
to land. These releases were primarily from rubber and
plastic hose industries . The largest releases (10% or
more of the total) occurred in Wisconsin and Tennessee.
ENVIRONMENTAL FATE
DEHP released to soil will neither evaporate nor leach
into groundwater. DEHP has a strong tendency to adsorb
to soil and sediments. Calculated log Koc values of 4 to
5 have been reported. Experimental evidence demon-
strates strong partitioning to clays and sediments (log K=
4-5). Limited data is available to suggest that it may
biodegrade in soil under aerobic conditions following
acclimation.
DEHP released to water systems will biodegrade fairly
rapidly (half-life 2-3 weeks) following a period of acclima-
tion. It will also strongly adsorb to sediments (log Koc 4 to
5). Evaporation and hydrolysis are not significant aquatic
processes.
Atmospheric DEHP will be carried long distances and
be removed by rain.
DEHP does have a tendency to bioconcentrate in
aquatic organisms; the experimental BCF values range
from a log of 2 to 4 in fish and invertebrates. In fathead
minnows the log BCF was 2.93; in bluegill sunfish it was
2.06.
Human exposure will occur in occupational settings
and from air, from consumption of drinking water, food
(especially fish etc, where bioconcentration can occur)
and food wrapped in PVC, as well as during blood
transfusions from PVC blood bags.
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at > 0.0006 mg/L
ANALYSIS:
REFERENCE SOURCE METHOD NUMBERS
EPA 600/4-88-039 506; 525.2
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
A EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
v
* Other sources of toxicological and environmental fate data include:
- Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
October 1995
Technical Version
Page 2
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United States
Environmental Protection
Agency
Office of Water
4601
EPA811-F-95-003Z-T
October 1995
National Primary Drinking
Water Regulations
Picloram
CHEMICAL/ PHYSICAL PROPERTIES
CAS NUMBER: 1918-02-1
COLOR/FORM/ODOR:
Colorless crystals or powder with a
chlorine-like odor; forms water soluble
salts
M.P.: 218-219° C - B.P.: _° C
VAPOR PRESSURE: 6.2x10'7 mm Hg, 25° C
OCTANOL/WATER PARTITION (Kow):
DENSITY/SPEC. GRAV.: N/A
N/A
SOLUBILITY: 430 mg/L of water at 25° C;
Soluble in water
SOIL SORPTION COEFFICIENT: ,
Koc average= 13; moderate mobility
in soil
ODOR/TASTE THRESHOLDS: N/A
BlOCONCENTRATlON FACTOR:
BCF=31 in fish; not expected to
bioconcentrate in aquatic organisms.
HENRY'S LAW COEFFICIENT:
N/A; negligible volatilization
TRADE NAMES/SYNONYMS:
4-amino-3,5,6-trichloropicolinic acid;
"Agent White"; Tordon
DRINKING WATER STANDARDS,
MCLG: 0.5 mg/L
MCL: 0.5 mg/L
HAL(child): 1-to 10-day: 20mg/L .',
Longer-term: 0.7 mg/L
HEALTH EFFECTS SUMMARY
Acute: EPA has found picloram to potentially cause
the following health effects from acute exposures at
levels above the MCL: damage to central nervous sys-
tem, weakness, diarrhea, weight loss.
Drinking water levels which are considered "safe" for
short-term exposures: Fora 10-kg (22 Ib.) child consum-
ing 1 liter of water per day, a one- to ten-day exposure to
20 mg/L or up to a 7-year exposure to 0.7 mg/L.
Chronic: Picloram has the potential to cause the
following health effects from long-term exposures at
levels above the MCL: liver damage.
Cancer: There is inadequate evidence to state whether
or not picloram has the potential to cause cancer from a
lifetime exposure in drinking water.
USAGE PATTERNS
Picloram is a systemic herbicide used in salt form for
controlling annual weeds on crops, and in combination
with 2,4-D or 2,4,5-T against perennials on non-crop-
lands for brush control.
Picloram is used to control bitterweed, knapweed,
leafy spurge, locoweed, larkspur, mesquite, prickly pear,
and snakeweed on rangeland in the western states.
EPA estimates that 300,000 Ibs. of picloram were
produced in the US in 1982.
RELEASE PATTERNS
Picloram is released to the environment primarily from
its application as a herbicide, and also during its produc-
tion and handling. Since picloram is not a listed chemical
in the Toxics Release Inventory, data on releases during
its manufacture and handling are not available.
ENVIRONMENTAL FATE ••-•-.
Picloram is the most persistent of the ehlorobenzoic
acid herbicides.
If picioram is released to soil it will not be expected to
adsorb to the soil and may leach to groundwater, a
conclusion supported by the detection of picloram in
some groundwater samples. However, picloram is an
aromatic aminet and some aromatic amines have been
.shown to.bind.to humic materials which may be present
in some moist soils; this binding may decrease leaching
processes. It will not be expected to hydrolyze or evapo-
rate from soils or surfaces, it may be subject to significant
biodegradation in soils and ground water, with reported
half-lives in soils ranging from 55-100 days or more.
If released to water it will not be expected to adsorb to
sediments, to evaporate, or to appreciably hydrolyze. It
will be subject to significant near surface photolysis with
reported half-lives ranging from 2.3-41.3 days. Based on
biodegradation in soils and groundwater, it may be sub-
ject to degradation in surface waters. As an aromatic
amine, its rate of degradation in water and soil may be
October 1995
Technical Version
Printed on Recycled Paper
-------
increased due to oxidation by free radicals, adsorption to
humic materials followed by oxidation, and catalytic
oxidation by cations, although no experimental data
specific to picloram were found.
If released to the atmosphere it will be subject to
significant deposition and washout due to its low vapor
pressure (will adsorb to particulate matter) and significant
water solubility. It may also be subject to significant direct
photolysis. The estimated vapor phase half-life in the
atmosphere is 12.21 days as a result of reaction with
photochemically produced hydroxyl radicals.
Picloram is not expected to bioconcentrate in aquatic
organisms based on a reported BCF of 31 in fish and
estimated BCFs of 1 to 20.
General human exposure will occur mainly through its
manufacture and use as a herbicide.
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at > 0.0001 mg/L
ANALYSIS:
REFERENCE SOURCE METHOD NUMBERS
EPA 600/4-88-039 515.1; 515.2; 555
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
A EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
4 Other sources of toxicological and environmental fate data include:
•Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
• National Pesticide Hotline - 800/858-7378
October 1995
Technical Version
Page 2
-------
United States
Environmental Protection
Agency
Office of Water
4601
EPA811-F-95-003aa-T
.October 1995
National Primary Drinking
Water Regulations
Polychlorinated Biphenyls (PCBs)
CHEMICAL/PHYSICAL PROPERTIES
CAS NUMBER: 1336-36-3
COLOR/ FORM/ODOR: PCB is generic term
for group of organic chemicals which
can be odorless or mildly aromatic
. solids or oily liquids; available in
mixtures containing several PCBs and
other organics as well.
M.P.: 340 io 375° C B.P.: N/A
OCTANOL/WATER PARTITION (Kow): N/A
VAPOR PRESSURE: N/A; moderately volatile
. from water and soil
DENSITY/SPEC. GRAV.: 1.44 at 30° C
SOLUBILITY: N/A; insoluble in water
SOIL SORPTION COEFFICIENT:
Koc generally above 5000; low
mobility in soil, but may leach with
mobile organic solvents.
ODOR/TASTE THRESHOLDS: N/A
BlOCONCENTRATION FACTOR:
Log BCF - 3.26 to 5.27 in aquatic
organisms; expected to bioconcentrate
in aquatic organisms.
HENRY'S LAW COEFFICIENT: • -,-.
3.3x10^4 to 5x10-5 atm-cu m/mole at 20
deg C
TRADE NAMES/SYNONYMS:
PCB, Chlorinated diphenyl, Clophen,
Kanechlpr, Aroclor, Fenclor, Chlorextol,
Dykanol, Inerteen, Monter, Pyralene,
Santotherm, sovol, Therminol, Noflambl
DRINKING WATER STANDARDS
MCLG: zero mg/L
MCL: 0.0005 mg/L ;
HAL(child): none
/ ___'•"
HEALTH EFFECTS SUMMARY
Acute: EPA has found PCBs to potentially cause the
following health effects from short-term exposures at
levels above the MCL: acne-like eruptions and pigmen-
tation of the skin; hearing and vision problems; spasms.
Chronic: PCBs have the potential to cause the
following health effects from long-term exposure at levels,
above the MCL: effects similar to acute poisonings;
irritation of nose, throat and gastrointestinal tracts;
lubricants, cutting oils, in heat transfer systems, carbon-
less reproducing paper. v
v ' ..-"'' " ' -
RELEASE PATTERNS
Current evidence suggests that the major source of
PCB release to the environment is an environmental
cycling process of PCBs previously introduced into the
environment; this cycling process involves volatilization
from ground surfaces (water, soil) into the atmosphere
with subsequent removal from the atmosphere via wet/
dry deposition andjhen revolatilization. PCBs are also
currently released to the environment from landfills con-
taining PCB waste materials and products, incineration
of municipal refuse and sewage sludge, and improper (or
cnanges in liver Tuncuon.
Cancer: There is some evidence that PCBs may have
the potential to cause cancer from a lifetime exposure at
levels above the MCL.
i
USAGE PATTERNS
Production of PCBs has decreased drastically: from
over 86 million Ibs. in 1970 to 35 million Ibs in 1977. EPA
banned most uses of PCBs in 1979. In 1975 it was
estimated that industries consumed PCBs as follows:
Capacitors, 70%; Transformers, 30%
PCBs were formerly used in the USA as hydraulic
fluids, plasticizers, adhesives, fire retardants, way ex-
tenders, dedusting agents, pesticide extenders, inks,
Toxic RELEASE INVENTORY -
RELEASES TO WATER AND LAND:
TOTALS (in pounds)
Top Five States
CA '
NJ
KY
WA
TN
Major Industries
Non-ferrous wire .
Steel pipe/tubing
Pulp mills
• mm • f
Water
784
0
0
250
0
255
0
'0
0
i 987 TO 1993
• m _ .- f
Land
73,632
58,178 '
13,188
• 750
998
251
58,178
'998
October 1995
Technical Version
Printed on Recycled Paper
-------
illegal) disposal of PCB materials, such as waste trans-
former fluid, to open areas.
From 1987 to 1993, according to EPA's Toxic Chemi-
cal Release Inventory, PCB releases to land and water
totalled over 74,000 IDS., of which about 99 percent was
to land. The bulk of these releases occurred in 1990 and
were primarily from non-ferrous wire drawing and insulat-
ing industries. The largest releases (10% or more of the
total) occurred in California.
ENVIRONMENTAL FATE
PCBs are mixtures of different congeners of
chlorobiphenyl and the relative importance of the envi-
ronmental fate mechanisms generally depends on the
degree of chlorination. In general, the persistence of
PCBs increases with an increase in the degree of chlori-
nation. Mono-, di- and trichlorinated biphenyls biode-
grade relatively rapidly, tetrachlorinated.biphenyls biode-
grade slowly, and higher chlorinated biphenyls are resis-
tantto biodegradation. Although biodegradation of higher
chlorinated congeners may occur very slowly on an
environmental basis, no other degradation mechanisms
have been shown to be important in natural water and soil
systems; therefore, biodegradation may be the ultimate
degradation process in water and soil.
If released to soil, PCBs experience tight adsorption
with adsorption generally increasing with the degree of
chlorination of the PCB. PCBs will generally not leach
significantly in aqueous soil systems; the higher chlori-
nated congeners will have a lowertendency to leach than
the lower chlorinated congeners. In the presence of
organic solvents PCBs may leach quite rapidly through
soil. Vapor loss of PCBs from soil surfaces appears to be
an importantfate mechanism with the rate of volatilization
decreasing with increasing chlorination. Although the
volatilization rate may be low, the total loss by volatiliza-
tion over time may be significant because of the persis-
tence and stability of PCBs. Enrichment of the low-CI
PCBs occurs in the vapor phase relative to the original
Aroclor; the residue will be enriched in the PCBs contain-
ing high Cl content
If released to water, adsorption to sediment and sus-
pended matter will be an important fate process; PCB
concentrations in sediment and suspended matter, have
been shown to be greater than in the associated water
column. Although adsorption can immobilize PCBs (es-
pecially the higher chlorinated congeners) for relatively
Jong periods of time, eventual resolution into the water
column has been shown to occur. The PCB composition
in the water will be enriched in the lower chlorinated PCBs
because of their greater water solubility, and the least
water soluble PCBs (highest Cl content) will remain
adsorbed. In the absence of adsorption, PCBs volatilize
relatively rapidly from water. However, strong PCB ad-
sorption to sediment significantly competes with volatil-
ization, with the higher chlorinated PCBs having longer
half-lives than the lower chlorinated PCBs. Although the
resulting volatilization rate may be low, the total loss by
volatilization overtime may be significant because of the
persistence and stability of the PCBs.
If released to the atmosphere, PCBs will primarily exist
in the vapor-phase; the tendency to become associated
with the particulate-phase will increase as the degree of
chlorination of the PCB increases. Tjie dominant atmo-
spheric transformation process is probably the vapor-
phase reaction with hydroxyl radicals which has esti-
mated half-lives ranging from 12.9 days for
monochlorobiphenyl to 1.31 years for
heptachlorobiphenyl. .Physical removal of PCBs from the
atmosphere, which is very important environmentally, is
accomplished by wet and dry deposition.
PCBs have been shown to bioconcentrate significantly
in aquatic organisms. Average log BCFs of 3.26 to 5.27,
reported for various congeners in aquatic organisms,
show increasing accumulation with the more highly chlo-
rinated congeners. The major PCB exposure routes to
humans are through food and drinking water, and by
inhalation of contaminated air.
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at congener-specific limits
ANALYSIS:
REFERENCE SOURCE . METHOD NUMBERS
EPA 600/4-88-039 505; 508; 508A
TREATMENT: .
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal >
FOR ADDITIONAL INFORMATION:
*• EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
* Other sources of lexicological and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
October 1995
Technical Version
Page 2
-------
United States
Environmental Protection
Agency
Office of Water
4601
EPA811-F-95-002bb-T
October 1995
National Primary Drinking
Water Regulations
Simazine
CHEMICAL/PHYSICAL PROPERTIES
CAS NUMBER: 122-34-9
COLOR/ FORM/ODOR:
White powder
M.P.: 225° C B.P.: N/A .
VAPOR PRESSURE: 6.1x1fJ-9
OCTANOL/WATER PARTITION (Kow):
Log Kpw = 2.18
DENSITY/SPEC. GRAV.: 1.3g/ml at 20° C BIOCONCENTRATION FACTOR:
SOLUBILITY: 5 mg/L of water at 20" C;
Soluble in water
ODOR/TASTE THRESHOLDS: N/A
SOIL SORPTION COEFFICIENT:
Koc =135 (measured); slight to high
mobility iii soil,,depending upon other
factors
HENRY'S LAW COEFFICIENT: -
4.63x1 CV10 atm-cu m/mole
BCF <10 in fish; not expected to
bioconcentrate in aquatic organisms.
TRADE NAMES/SYNONYMS:
Aktinit; Batazina; Bitemol;
CAT(Herbicide); CDT; Cekuzina-S;
Geigy 27,692; Gesatop; Herbaziri;
Herbex; Hungazin; Premazine; Primatpl
S; Pricep; Printop; Radocon; Simadex;
Tafazine; Zeapur; 2-chloro-4,6-
bis(ethylamino)-1,3,5-Triazine
DRINKING WATER STANDARDS
MCLG: 0.004 mg/L
MCL: 0.004 mg/L
HAL(child): 1-to 10-day: 0.07 mg/L
Longer-term: 0.07 mg/L
HEALTH EFFECTS SUMMARY
Its major use is on corn where it is often combined with
AAtrex. Other herbicides with which simazine is com-
bined include: paraquat, on apples, peaches; Roundup
or Oust for noncrop use; Surflan on Christmas trees; Dual
on corn and ornamentals.
The amount of simazine used annually in the USA was
estimated in 1985 to be 4.8 billion pounds.
Acute: EPA has found simazine to potentially cause RELEASE PATTERNS
the following health effects from acute exposures at simazine may be released into the environment via
levels above the MCL: weight loss, changes m blood. effluents at manufacturing sites and at points of applica-
Drinking water levels which are considered "safe" for tion where it is employed as a herbicide.
shott-terrrvexposures: For a 10-kg (22 Ib.) child consum- Sjnce simazine fs not a |jsted ehemica| ,in the Toxics
ing Irter of waterper day, up to a 7-year exposureto 0.07 Re|ease inventory, data on releases during its manufac-
mg . ture and handling are not available.
Chronic: Simazine has the potential to cause the .
following health effects from long-term exposures at ENVIRONMENTAL FATE
levels above the MCL: tremors; damage to testes, kid- |f released to water, simazine is not expected to adsorb
neys, liver and thyroid; gene mutations. to sediment and suspended paniculate matter, or to
Cancer: There is some evidence that simazine may volatilize. Persistence depends upon many factors in-
havethe potential to cause cancer from a lifetime expo- eluding degree of algae and weed infestation. Simazine
sure at levels above the MCL. residues may persist up to 3 years in soil under aquatic
field conditions. Dissipation of simazine in pond and lake
USAGE PATTERNS ' water was variable, with half-lives ranging from 50 to 700
.. days. Slow biodegradation of simazine may occur in
Simazine is a pre-emergence herbicide used for con- water based upon tne s,ow biodegradation observed in
trol of broad-leaved and grassy weeds on a variety of soi| simazine is fairly resistant to hydrolysis. However,
deep-rooted crops such as artichokes, asparagus, berry chemica| hydrolysis of simazine may be more important
crops, broad beans, citrus, pome and stone fruits or- environmentally than biodegradation at low pH or when
chards, and others. It is also used on non-crop areas various catalysts are present.
such as farm ponds, fish hatcheries, etc.
October 1995
Technical Version
Printed on Recycled Paper
-------
If released to soil, the mobility of simazine will be
expected to vary from slight to high in soil-types ranging
from clay soils to sandy loams soils, respectively, based
upon soil column, soil thin-layer chromatography, and
Koc experiments. Therefore, it may leach to groundwa-
ter; adsorption of simazine in soil has been observed to
increase as titratable acidity, organic matter and, to a
lesser extent, clay content of the soil increased.
Simazine may be susceptible to slow hydrolysis in soil
based upon reported half-lives for degradation (purport-
edly mainly soil catalyzed hydrolysis) of simazine in two
soil 45 and 100 days.
Simazine can be utilized by certain soil microorgan-
isms as a source of energy and mineralization. No
degradation of simazine was detected in a soil suspen-
sion test without the addition of glucose as an energy
source suggesting that degradation of simazine in these
soil experiments was due to co-metabolism. Reported
persistence of simazine in soil varies from a half-life of <1
month to no degradation being observed in 3.5 months.
Simazine is not expected to volatilize from near surface
soils or surfaces under normal environmental conditions.
If released to the atmosphere, simazine is expected to
exist almost entirely in the particulate phase. Vapor
phase reactions with photochemically produced hydroxyl
radicals in the atmosphere may be important (estimated
half-life of about 2.8 hr). Photolysis may be an important
removal mechanism in the atmosphere.
Simazine has a low potential to bioaccumulate in fish.
BCFs: 0.76-0.95, green sunfish ; <1, bluegill sunfish; 5,
bluegill sunfish; 2, catfish. Other BCF values up to 55
have been reported in the literature.
The most probable exposure should be occupational
exposure which may occur through dermal contact or
inhalation at places where simazine is produced or used
as a herbicide.
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at> 0.00007 mg/L
METHOD NUMBERS
505; 507; 508.1; 525.2
ANALYSIS:
REFERENCE SOURCE
EPA 600/4-88-039
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
FOR ADDITIONAL INFORMATION:
4 EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
4 Other sources of lexicological and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
•.Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
• National Pesticide Hotline - 800/858-7378
October 1995
Technical Version
Page 2
-------
United States
Environmental Protection
Agency
Office of Water
4601
EPA 811-F-95-0033C-T
October 199E
National Primary Drinking
Water Regulations
Toxaphene
CHEMICAL/PHYSICAL PROPERTIES
CAS NUMBER: 8001-35-2
COLOR/ FORM/ODOR:
Amber waxy solid with a piney odor; a
mixture of pdlychlorinated compounds,
available as a dust, wettable powder,
or as emulsifiable or oil solutions
M.P.: 65-90°C B.P.: Decomposes
VAPOR PRESSURE: 0.4 mm Hg at 25° C
OCTANOL/WATER PARTITION (Kow):
Log Kow = 3.3
DENSITY/SPEC. GRAV.: 1.65 at 25° C
SOLUBILITY: 3 mg/L of water at 22° C;
Slightly soluble in water
SOIL SORPTJON COEFFICIENT:
Koc = 2.1x10s; very low mobility in soil
ODOR/TASTE THRESHOLDS: Odor thresh-
old in water is 0.14 mg/L
BIOCONCENTRATION FACTOR:
BCFs of 3100 to 69,000 in fish; high
potential to bioconcentrate in aquatic
organisms. ~
HENRY'S LAW COEFFICIENT:
-0.063 to 0.005 atm-cu m/mole; will
volatilize from water/soil
TRADE NAMES/SYNONYMS:
Chlorinated camphene,
Octachlorocamphene, Camphochlor,
Agricide Maggot Killer, Alltex, Crestoxo,
. Compound 3956, Estonox, Fasco-
Terpene, Genipherie, Hercules 3956,
M5055, Melipax, Motox, Penphene,
Phenacide, Phenatox, Strobane-T,
Toxadust, Toxakil, Vertac 90%, toxon
63, Attac, Anatpx, Royal Brand Bean
Tox 82, Cotton Tox MP82, Security Tox-
Sol-6, Security Tox-MP cotton spray,
Security Motox 63 cotton spray, Agro-
Chem Brand Torbidan 28, Dr Roger's
TOX-ENE
DRINKING WATER STANDARDS
MCLG: zero mg/L
MCL: 0.003 mg/L
HAL(child): none
HEALTH EFFECTS SUMMARY i
Acute: EPA has found toxaphene to potentially cause
the following health effects from acute .exposures at
levels above the MCL: central nervous system effects
including restlessness, hyperexcitability, tremors, spasms
or convulsions.
EPA has not set drinking water levels which are consid-
ered "safe" for short-term exposures. .
Chronic: Toxaphene has the potential to cause the
following health effects from long-term exposures at
levels above the MGL: liver and kidney degeneration;
central nervous system effects; possible immune system
suppression.
Cancer: There is some evidence that toxaphene may
have the" potential to cause cancer from a lifetime
exposure at levels above the MCL.
USAGE PATTERNS '
Production of toxaphene in 1977 was nearly 40 million
pounds. By 1982, when EPA cancelled most of its uses,
consumption was reported at 12 million pounds.
Toxaphene was used as an insecticide for cotton
(50%), vegetables (17%), livestock and poultry (17%),
soybeans (12%), alfalfa, wheat and sorghum (5%).
All formulations are now Restricted Use Pesticides.
Special livestock formulations are available & recom-
,rhended for the control of scab mites or mange on
livestock. Rigo Toxaphene 6 has been registered for
sicklepod control in AL, GA, MS, AR, NC, SC, & TN as
24(C) registrations for speciallocal needs. Strobajie T-
90 has a broad spectrum activity as stomach & contact
residual insecticide, & it has shown activity against sev-
eral species of worms, scab, mites, homflies, lice &
mealybugs & major cotton insects. In the past, it has been
used as piseicide (fish toxicant) in lakes. ,
Other minor uses: for armyworms, cutworms, & grass-
hoppers; for mealybug & pineapple gummosis moth
control on pineapples & weevil control on bananas.
Conditional and restricted use as an insecticide and as a
rhiticide in foliar treatment of: cranberries, strawberries,
apples, pears, quinces, nectarines, peaches, bananas,
pineapple, eggplant, peppers, pimentos, tomatoes, broc-
coli, brussel sprouts, cabbage, cauliflower, collards, kale,
kohlrabi, spinach, lettuce (head and leaf), parsnips, ruta-
bagas, beans (lima, green and snap), corn (sweet),
cowpeas, okra, alfalfa, barley, oats, rice, rye, wheat,
celery, cotton, horseradish, peanuts, peas, sunflowers,
soybeans, ornamental plants, birch, elm, hickory, maple,
oak, arid noncrop areas. Also used in seed crop foliar
October 1995
Technical Version
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treatment of clover and trefoil; in soil treatment of corn; in tial. Chickens fed 5,50, or 100 ppm toxaphene in the diet,
back rubber of beef cattle; in animal treatment of goats, residues are detected in eggs and adipose tissue with a
sheep, beef cattle, and hogs; and aerial application and BCF of about 5.
tank mixtures. Monitoring data demonstrates that toxaphene is a
contaminant in some air, water, sediment, soil, fish and
RELEASE PATTERNS other aquatic organisms, foods and birds. Human expo-
Toxaphene is released into the environment primarily sure aPPears to come most|y from food or occupational
from its application as an insecticide forthe protection of exP°sure-
cotton, mostly in southern states.
ENVIRONMENTAL FATE
Toxaphene is very persistent. When released to soil it
will persist for long periods (1 to 14 yr), is not expected to
leach to groundwater or be removed significantly by
runoff unless adsorbed to clay particles which are re-
moved by runoff. In water itwill not appreciably hydrolyze,
photolyze, or significantly biodegrade. It will strongly sorb
to sediments.
Little information concerning biodegradation of toxa-
phene in aquatic systems was found in the literature.
However, it has been reported that the detoxification of
toxaphene was due to adsorption rather than by degra-
dation in 8 Wisconsin lakes. Degradation in aquatic
sediment was more significant under anaerobic than
aerobic conditions and oxidative as well as reductive
metabolism can be important in the degradation of toxa-
phene. Anaerobic conditions in sediments led to nearly
50% overall degradation of 3 main components of toxa-
phene; under aerobic conditions 13.6% degradation of
the 3 components was observed- Toxaphene is resistant
to degradation in soils with reported half-lives ranging
from 0.8 yrto 14 yr. 50% loss in 6 weeks due to biological
transformation in anaerobic, flooded soils was reported
while no transformation was found in aerobic sediments.
Evaporation from soils and surfaces will be a signifi-
cant process for toxaphene. Based on range of reported
Henry's Law constants the calculated range of the half-
life for evaporation of toxaphene from a model river is 6.0-
6.3 hr. Although toxaphene is strongly adsorbed to soil,
evaporation from soils may be a significant process.
Evaporation losses of from 7 to 14 kg/ha/yr or more have
been estimated from loam soil under annual rainfall of
150 cm. Field studies have shown it to be detoxified
rapidly in shallow and very slowly in deep bodies of water.
Toxaphene may undergo very slow direct photolysis in
the atmosphere. However vapor phase reactions with
photochemically produced hydroxyl radicals should be
more importantfate process (estimated half-life4-5 days).
Toxaphene can be transported long distances in the air
(1200 km) probably adsorbed to particular matter.
Bioconcentration factors (BCF) forfish - 3100 to 69,000;
for shrimp 400-1200; Algae - 6902; snails - 9600. These
BCF values indicated significant bioconcentration poten-
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES: •
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:.
2 quarterly per year if serving >3300 persons;
• 1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at > 0.001 mg/L
ANALYSIS:
REFERENCE SOURCE METHOD NUMBERS
EPA 600/4-88-Q39 ' 505; 508; 525.2
TREATMENT:
BEST AVAILABLE TECHNOLOGIES
Granular Arfivated Charcoal
FOR ADDITIONAL INFORMATION:
A EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
* Other sources of toxicclogical and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Releasejnventory, National Library of Medicine - 301/496-5531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
• National Pesticide Hotline - 800/858-7378
October 1995
Technical Version
Page 2
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United States
Environmental Protection
Agbncy
Office of Water
4601
EPA811-F-95-003dd-T
October 1995
National Primary _
Water Regulations
2,4,5 - TP (Silvex)
CHEMICAL/PHYSICAL PROPERTIES
CAS NUMBER: 93-72-1
COLOR/FORM/ODOR:
White powder with little odor; available
in granules, solutions and tablets as
the amine or sodium emulsifiable salts
& various esters.
M.P.: 181.6° C B.P.: N/A
VAPOR PRESSURE: N/A
OCTANOL/WATER PARTITION (Kow): N/A
DENSITY/SPEC. GRAV.: 1.21 at 20° C
SOLUBILITY: 200 mg/L of water at 25? C;
Slightly soluble in water
SOIL SORPTION COEFFICIENT:
Koc reported at 2600; Very low
mobility in soil
ODOR/TASTE THRESHOLDS: N/A
HENRY'S LAW COEFFICIENT: N/A
BlOCONCENTRATION FACTOR:
BCF=58 in fish; not expected to
bioconcentrate in aquatic organisms.
TRADE NAMES/SYNONYMS:
2,4,5-Trichlorophehoxyproprionic acid;
Weed-B-Gon; Proppn; Silvi-Rhap; Sta-
fast; Miller Nu Set; Aqua-Vex;
Color-Set; Ded-Weed; Fenoprop;
Fenormone; Fruitone T; Garlon; Kuran;
Kurosal G/SL; Silvex
DRINKING WATER STANDARDS
MCLG: 0.05 mg/L
Mci_: 0.05 mg/L
HAL(child): 1^ to 10-day: 0.2 mg/L
Longer-term: 0.07 mg/L
HEALTH EFFECTS SUMMARY
Acute: EPA has found 2,4,5-TP to potentially cause
the following health effects from acute exposures at
levels above the MCL: depression and other nervous
system effects, weakness, stomach irritation and minor
damage to liver and kidneys.
Drinking water levels which are considered "safe" for
short-term exposures: Fora 10-kg (22 Ib.) child consum-
ing 1 liter of water per day, a one- to ten-day exposure to
0.2 mg/L or upto a 7-year exposure to 0.07 mg/L.
Chronic: 2,4,5-TP has the potential to cause the ENVIRONMENTAL FATE
following health effects from long-term exposures at
levels above the MCL: minor liver and kidney damage
however, silvex is not used in the U.S. due to the
cancellation of all registered uses effective Jan 2,1985.
the greatest use of 2,4,5-TP was as,a postemergence
herbicide for control of woody plants, and broadleaf
herbaceous weeds in rice and bluegrass turf, in sugar-
cane, in rangeland improvement programs, on lawns.
Aquatic uses include control of weeds in: ditches and
riverbanks, on floodways, along canals, reservoirs,
streams, and along southern waterways.,
RELEASE PATTERNS
Former sources of release include spraying from appli-
cation of the herbicide formulations, runoff from fields,
and direct release to water for control of aquatic weeds.
It may also have been released as the result of hydrolysis
of esters of silvex.
Cancer: There is inadequate evidence to state whether
or not 2,4,5-TP has the potential to cause cancer from a
lifetime exposure in drinking water. >
USAGE PATTERNS
In 1982, 2,4,5-TP production was 500,000 pounds,
with industrial/commercial herbicide consuming.60%;
range and pastureland use consuming 40%. The amount
of silvex used annually in the U.S. prior to 1983 Was
estimated in 1985 to be 7,000 pounds. At present,
When released on land, silvex will strongly adsorb to
soils and biodegrade, but is not expected to leach,
hydrolyze, or evaporate. It may be lost due to runoff frorn
treated fields. Silvex has been reported to be very well
adsorbed to essentially completely adsorbed in soils
(reported Koc Value of 2600). Average half-lives for
biodegradation of silvex in soils ranged from 12 days for
3 prairie soils to 17 days. Negligible degradation was
observed in air-dried soils.
. If released to water, silvex will biodegrade slowly and
strongly adsorb to sediment, where slow biodegradation
will occur. The loss due to volatilization of silvex from
October 1995
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aqueous and soil systems will not be significant due to its
low vapor pressure of the acid. It will not appreciably
hydrolyze but may be subject to photooxidation near the
surface of waters.
While no data concerning the rate of biodegradation in
water were found, available information suggests that
silvex is degraded slowly both in water and sediments.
2,4,5-Trichlorophenol has been identified as a product of
the biodegradation of silvex. From limited data available,
it may be concluded that any phenoxy herbicide, whether
applied as ester or as dimethylamine salt formulations,
may be chemically transformed to the same
phenoxyalkanoic anion in soil and water at rates depen-
dent on pH. These anions would presumably reassociate
with a variety of inorganic cations present in the soil to
maintain electrical neutrality, and then undergo leaching
and biological degradation.
Silvex may be released to air during spraying opera-
tions but not as a result of evaporation due to its very low
vapor pressure. It will be lost from the atmosphere mainly
by rainout and dry deposition. Vapor phase photooxida-
tion by reaction with photochemically produced hydroxyl
radicals may be significant (estimated half-life 6.3 hrs).
Bioconcentration of silvex will not be significant based
with a reported bioconcentration factor of 58 for fish in
flowing water.
Agricultural workers may have been exposed to silvex
during spraying operations using herbicides containing
this chemical. Exposure may have also occurred through
consumption of contaminated foods, including fruits and
milk. At present, however, no Workers are expected to be
exposed to silvex during application of herbicides be-
cause all registered uses of silvex were canceled effec-
tive Jan 2, 1985.
OTHER REGULATORY INFORMATION
MONITORING:
FOR GROUND/SURFACE WATER SOURCES:
INITIAL FREQUENCY- 4 quarterly samples every 3 years
REPEAT FREQUENCY- If no detections during initial round:
2 quarterly per year if serving >3300 persons;
1 sample per 3 years for smaller systems
TRIGGERS - Return to Initial Freq. if detect at > 0.0002 mg/L
ANALYSIS:
REFERENCE SOURCE METHOD NUMBERS
EPA 600/4-88-039 515.1; 515.2; 555
TREATMENT: '
BEST AVAILABLE TECHNOLOGIES
Granular Activated Charcoal
Fo/? ADDITIONAL INFORMATION:
4 EPA can provide further regulatory and other general information:
• EPA Safe Drinking Water Hotline - 800/426-4791
* Other sources of lexicological and environmental fate data include:
• Toxic Substance Control Act Information Line - 202/554-1404
• Toxics Release Inventory, National Library of Medicine - 301/496-6531
• Agency for Toxic Substances and Disease Registry - 404/639-6000
• National Pesticide Hotline - SOO/858-7378 ,
October 1995
Technical Version
Page 2
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