National Primary Drinking Water Regulations Technical Factsheet on: DI (2-ETHYLHEXYL) ADIPATE 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 Acute: EPA has no data on the acute toxicity of di (2-ethylhexyl) adipate, or DEHA, which is relevant to the drinking water context. Drinking water levels which are considered "safe" for short-term exposures for a 10-kg (22 lb.) 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 shadow, cologne, foundations, rouge, blusher, nail-polish remover, moisturizers and indoor tanning preparations; 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-owned treatment works (POTW) and chemical manufacturing plants. Adipates are also used as a plasticizer in PVC materials and is known to leach from plumbing made of PVC plastic. Thus, adipates have been recognized as a potential drinking water contaminant. From 1987 to 1993, according to EPA's Toxic Chemical Release Inventory, adipate releases to land and water totalled over 450,000 lbs., 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 environmentally 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 approximately 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 important environmentally but may be important in aquatic organisms that are unable to metabolize adipate. Occupational exposure can occur through dermal contact and inhalation. The general population can be exposed 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. Chemical/ Physical Properties CAS Number: 103-23-1 Color/ Form/Odor: Light colored, oily liquid with an aromatic odor M.P.: -67.8ø C B.P.: 214ø C Vapor Pressure: 8.5x10-7 mmHg at 25ø C Octanol/Water Partition (Kow): Log Kow = >6.11 Density/Spec. Grav.: 0.922 at 25ø C Solubility: 0.78 g/L of water at 22ø C; Slightly soluble in water Soil sorption coefficient: Koc estimated at 5004 to 48,000; immobile in soil Odor/Taste Thresholds: N/A Bioconcentration Factor: BCF = 27 in fish; not expected to bioconcentrate in aquatic organisms. Henry's Law Coefficient: 4.34x10-7 atm-cu m/mole at 20ø C; Trade Names/Synonyms: Adipic acid, bis(2-ethylhexyl) ester; Bis(2-ethylhexyl) hexanedioate; BEHA; DEHA; Adipol 2EH; Bisoflex 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; Kemester 5652; Reomol DOA; Rucoflex plasticizer DOA; Staflex DOA. Adipate, (2-diethylhexyl) 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 Toxic Release Inventory - Releases to Water and Land, 1987 to 1993 (in pounds): Water Land TOTALS 27,471 425,230 Top Five States* OH 531 173,900 IN 5,500 93,275 VA 1,886 46,102 TN 18,480 26,409 MI 250 29,750 Major Industries* Gray iron foundries 2,263 316,438 Aluminum foundries 250 50,409 Rubber, plastic hose/belts 10 32,078 Space propulsion units 0 20,363 Misc Indust. organics 11,996 131 * Water/Land totals only include facilities with releases greater than a certain amount - usually 1000 to 10,000 lbs. For Additional Information: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 National Primary Drinking Water Regulations Technical Factsheet on: ALACHLOR 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 Acute: EPA has found alachlor to potentially cause slight skin and eye irritation from acute exposures at levels above the MCL. Drinking water levels which are considered "safe" for short-term exposures: For a 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 exposure 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%). Application 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. 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 concentrations above the MCL in at least 15 States. Environmental Fate In soil, alachlor is transformed to its metabolites primarily by biodegradation. The half-life of alachlor disappearance 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 continuous 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 decrease 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 alachlor will be lost from treated field. The estimated half-life of alachlor evaporation from soil is in the range 12 to >200 days. In water, both photolysis and biodegradation are important 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 groundwater may be due to less microbial activity or the absence of alachlor degraders in anaerobic samples. The measured and estimated Henry's Law constant (H) for alachlor at ambient temperatures is in the range 3.2X10-8 to 1.2X10-10 atm-cu m/mole, 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 alachlor will 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 of fish 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 elimination of alachlor from the leaves starting at 15 days. Chemical/ Physical Properties CAS Number: 15972-60-8 Color/ Form/Odor: Available in granular, emulsifiable concentrate and flowable formulations M.P.: 40-41ø C B.P.: N/A Vapor Pressure: Negligible Density/Spec. Grav.: 1.133 at 25ø C Octanol/Water Partition (Kow): Log Kow = 2.63 and 3.53 Solubility: 0.14 g/L of water at 23ø C; Slightly soluble in water Soil sorption coefficient: Koc = 2.08 to 2.28; medium to highmobility in soil Odor/Taste Thresholds: N/A Bioconcentration 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 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 600/4-88-039 505; 507; 525.2; 508.1 Treatment- Best Available Technologies: Granular Activated Charcoal For Additional Information: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: ALDICARB AND METABOLITES Drinking Water Standards (in mg/L) MCLG MCL HAL(child) Aldicarb 0.001 0.003 none Aldicarb Sulfone 0.001 0.003 none Aldicarb Sulfoxide 0.001 0.004 none NOTE: The MCLs for aldicarb and its metabolites are presently stayed. Health Effects Summary Acute: EPA has found aldicarb to potentially cause nausea, diarrhea and relatively minor neurological symptoms resulting from acute exposures at levels above the MCL. These effects appear to be rapidly and completely reversible after exposure. No Health Advisories have been established for short-term exposures. Chronic: Aldicarb has the potential to cause neurological effects such as sweating, pupillary constriction and leg weakness from chronic exposure at levels above the MCL. These effects are associated with the inhibition of cholinesterase in blood and nerve tissue. Cancer: There is inadequate evidence to state whether or not either aldicarb or its metabolites have the potential to cause cancer from lifetime exposures in drinking water. Usage Patterns Aldicarb is applied to the soil for control of chewing & sucking insects (aphids, whiteflies, leaf miners, soil-dwelling insects), spider mites, and nematodes. It is used in glasshouse & outdoor ornamentals, and on the following crops; cotton, sugar beet, fodder beet, strawberries, potatoes, onions, hops, vine nurseries, tree nurseries, groundnuts, soya beans, citrus fruit, bananas, coffee, sorghum, pecans, sweet potatoes & other crops. Cotton crops account for 83% of aldicarb use. As the result of the aldicarb contamination of drinking water wells, Union Carbide Corporation excluded the use of aldicarb products in Suffolk County, Long Island, New York. The company also limited the use of aldicarb products to once every two years and only after plant emergency in the States of Maine and Wisconsin and the Counties of Hartford in Connecticut, Kent and New Castle in Delaware, Franklin and Hampshire in Massachusetts, Worchester in Maryland, Atlantic, Burlington, Cumberland, Monmouth and Salem in New Jersey, Newport and Washington in Rhode Island, and Accomack and Northampton in Virginia. Aldicarb may be applied at planting at the 1 lb active ingredient/acre rate for aphid control in the State of Maine. Release Patterns Release of aldicarb to the environment will occur due to its manufacture and use as a systemic insecticide, acaricide and nematocide for soil use. Environmental Fate If aldicarb is released to the soil it should not bind to the soil. It will be susceptible to chemical and possibly biological oxidation to form its metabolites, aldicarb sulfoxide and aldicarb sulfone. Hydrolysis is both acid and base catalyzed with examples of hydrolysis half-lives in soil at 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 previously treated with carbofuran. If aldicarb is released to water it should not adsorb to sediments or bioconcentrate in aquatic organisms. Aldicarb does not degrade in groundwater under aerobic conditions unless relatively high pH (pH 8.5) exists; reported half-lives in groundwater under anaerobic conditions at pH 7.7-8.3 were 62-1300 days. Aldicarb has been shown to be formed from aldicarb sulfoxide in groundwater under aerobic conditions and under anaerobic 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 estimated 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 reported and estimated BCF, aldicarb should not bioconcentrate in aquatic organisms. Chemical/ Physical Properties CAS Number: 116-06-3 Color/ Form/Odor: White crystals with slightly sulfurous odor; Available in granular formulations containing 5 to 15% aldicarb M.P.: 99-100ø C B.P.: N/A Vapor Pressure: 1x10-4 mm Hg at 25ø C Octanol/Water Partition (Kow): Log Kow = 1.13 Density/Spec. Grav.: 1.2 at 25ø C Solubility: 17 ug/L of water at 25ø C Soil sorption coefficient: Koc ranges from 8-37; high to very high mobility in soil Odor/Taste Thresholds: N/A Bioconcentration Factor: 42 in fish; not expected to bioconcentrate in aquatic organisms. Henry's Law Coefficient: 1.5x10-9 atm-cu m/mole; Trade Names/Synonyms: Temik; Carbamyl; Carbanolate; Sulfone aldoxycarb; Union Carbide 21149 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: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: ATRAZINE 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: For a 10-kg (22 lb.) child consuming 1 liter of water per day, a one- to ten-day exposure to 0.1 mg/L or upto a 7-year exposure to 0.05 mg/L. Chronic: Atrazine has the potential to cause weight loss, cardiovascular damage, retinal and some muscle degeneration, and mammary tumors from a lifetime exposure at levels above the MCL. Cancer: There is some evidence that atrazine may have the potential to cause cancer from a lifetime exposure at levels above the MCL. Usage Patterns Atrazine is a widely used herbicide for control of broadleaf and grassy weeds in corn, sorghum, rangeland, 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 and 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 Pesticides 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 degradation 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. 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. Atrazine 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 constituents. Adsorption is not irreversible, and desorption often occurs readily, depending on such factors as temperature, moisture, and pH. Photolysis of atrazine did not occur in water at wavelengths > 300 nm. At wavelengths greater than or equal to 290 nm, the photolysis half-life of atrazine at a concentration 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 concentration 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 2.63X10-9 atm-cu m/mole, which indicates volatilization 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 atmospheric concentration of 5X10+5 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 bioconcentration factor predicted from water solubility = 86 (calculated); predicted from soil adsorption coefficient = 7 (calculated). Chemical/ Physical Properties CAS Number: 1912-24-9 Color/ Form/Odor: Available as suspension concentrate; wettable powder; water-dispersible granules. M.P.: 171-174ø C B.P.: N/A Vapor Pressure: 3x10-7 mm Hg at 20ø C Density/Spec. Grav.: 1.19 g/mL at 20ø C Octanol/Water Partition (Kow): Log Kow = 2.75 Solubility: 0.03 g/L of water at 20ø C Odor/Taste Thresholds: N/A Soil sorption coefficient: Koc average is 122; medium to high mobility in soil Bioconcentration 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/mole (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 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 600/4-88-039 505; 507; 508.1; 525.2 Treatment- Best Available Technologies: Granular Activated Charcoal For Additional Information: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: POLYCYCLIC AROMATIC HYDROCARBONS (PAHs) Drinking Water Standards MCLG: zero mg/L Mcl: 0.0002 mg/L HAL(child): none Health Effects Summary Acute: EPA has found polycyclic aromatic hydrocarbons (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)pyrene 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 exposure at levels above the MCL. Usage Patterns Benzo(a)pyrene is one of a group of compounds called polycyclic aromatic hydrocarbons (PAHs), or polynuclear aromatic hydrocarbons (PNAs). They are not produced or used commercially but are ubiquitous in that they are formed as a result 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 charcoal-broiled; in incinerators, coke ovens, and asphalt processing and use. There are two major sources of PAHs in drinking water: 1) contamination of raw water supplies from natural and man-made 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 distribution systems. Though few data are available for estimating 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 environmental concentrations are highest near sources, its presence in places distant from primary sources indicates that it is reasonably stable in the atmosphere and capable of long distance transport. When released to air it may be subject to direct photolysis, although adsorption to particulates apparently can retard this process. It may 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 radicals 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 significant 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 biodegradation. BaP will be expected to undergo significant photodegradation near the surface of waters. Evaporation may be significant with a predicted half-life of 43 days. However, adsorption to sediments and particulates may significantly retard biodegradation, photodegradation, and evaporation. If released to soil it will be expected to adsorb very strongly and will not be expected to leach to the groundwater. 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 important 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; Bluegills, 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 metabolic 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 contaminated 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). Chemical/ Physical Properties CAS Number: 50-32-8 Color/ Form/Odor: Pale yellow needlelike crystals, faintly aromatic M.P.: 179-179.3ø C B.P.: >360ø C Vapor Pressure: >1 mm Hg at 20ø C Density/Spec. Grav.: 1.35 at 15ø C Octanol/Water Partition (Kow): Log Kow = 6.04 Solubility: 0.0038 mg/L of water at 25ø 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 metabolize it. Henry's Law Coefficient: N/A; volatilization not significant Trade Names/Synonyms: 3,4-Benz(a)pyrene; BaP; BP 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: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 National Primary Drinking Water Regulations Technical Factsheet on: CARBOFURAN 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 carbofuran to potentially cause a variety of nervous system effects from acute exposures, including: headache, sweating, nausea, diarrhea, chest pains, blurred vision, anxiety and general muscular weakness. These effects are largely due to carbofuran's rapid inhibition of cholinesterase activity, and is generally reversible once exposure ceases. Drinking water levels which are considered "safe" for short-term exposures: For a 10-kg (22 lb.) child consuming 1 liter of water per day, upto a 7-year exposure to 0.05 mg/L. Chronic: Available data on chronic toxic effects from oral exposures to carbofuran have shown that low doses of carbofuran appear to have little or no adverse health effects. Higher doses have the potential to cause damage to the nervous and reproductive systems. Cancer: There is no evidence that carbofuran has the potential to cause cancer from lifetime exposures in drinking water. Usage Patterns A 1984 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 rootworm. After September 1994, carbofuran will be allowed for use on only five U.S. crops: bananas (in Hawaii); pumpkins, cucumbers, watermelons, cantaloupes and squash; dry harvested cranberries,; pine progeny tests; and spinach grown for seed. Carbofuran will soon be banned from use on corn and sorghum in California. Release Patterns Carbofuran enters surface water as a result of runoff from treated fields and enters ground water by leaching of treated crops. EPA's 1990 National Pesticide Survey did not detect carbofuran levels above the MCL in rural domestic wells or Community Water System wells. EPA's Pesticides in Ground Water Database reports few detections of carbofuran in ground water between 1971 and 1991. Environmental Fate 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 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 water table aquifers beneath sandy soils in NY and WI. 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 hydrolysis 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 degradation by soil microbes, aquatic microbes may also be able to degrade carbofuran. The half-lives for degradation of carbofuran in different waters ranges from several hours to a few weeks. Aquatic volatilization, adsorption, and bioconcentration are not expected to be important. 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 atmosphere. Chemical/ Physical Properties CAS Number: 1563-66-2 Color/ Form/Odor: White crystalline solid with a slightly phenolic odor. Available as a flowable paste or wettable powder. M.P.: 153-154ø C B.P.: N/A Vapor Pressure: 3.4x10-6 mm Hg at 26.1ø C Octanol/Water Partition (Kow): Log Kow = 2.32 Density/Spec. Grav.: 1.18 at 20ø C Solubility: 0.7 g/L of water at 25ø 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 of fish; 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 or 3G, Brifur, Crisfuran, Chinufur, Curaterr, Yaltox, Pillarfuran, Kenofuran, 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 > 0.0009 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: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: CHLORDANE Drinking Water Standards MCLG: Zero mg/L MCL: 0.002 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, convulsions, 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: For a 10-kg (22 lb.) child consuming 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 exposure 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 ornamentals; 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 degradation 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 NJ and elsewhere indicates that movement to groundwater 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 suggested that chlordane is very slowly biotransformed in the environment which is consistent with the long persistence periods observed under field conditions. If released to water, chlordane is not expected to undergo significant hydrolysis, oxidation or drect photolysis. 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. However, 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 suggests that chlordane may be very persistent in the adsorbed 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 expected to exist predominately in the vapor phase. Chlordane 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 reservoir 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. 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.: 103-108ø C B.P.: 175ø C Vapor Pressure: 1x10-5 mm Hg at 25ø C Octanol/Water Partition (Kow): Log Kow = 2.78 Density/Spec. Grav.: 1.59-1.63 at 25ø C Solubility: 0.0001 g/L of water at 25ø 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 Henry's Law Coefficient: 1.3x10-3 atm-cu m/mole (gamma-chlordane) Bioconcentration 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-Kil, Cortilan-Neu, Dowchlor, Oktachlor, Oktaterr, Synklor, Tat Chlor 4, Topiclor, Toxichlor, Intox 8, Gold Crest C-100, Kilex, Kypchlor, Niran, Termi-Ded, Prentox, Pentiklor. 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 600/4-88-039 505; 508; 508.1; 525.2 Treatment- Best Available Technologies: Granular Activated Charcoal For Additional Information: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: 2,4 - D 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 nervous system damage from short-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 lb.) 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 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 lbs. in 1978 to 45.1 million lbs in 1982. 1991 data indicates only that production exceeded 5000 lbs. 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 Chemical Release Inventory, 2,4-D releases to land and water totalled over 116,000 lbs., most of which was released to land. These releases were primarily from cane sugar-related industries (except refineries). The largest releases (10% or more of the total) occurred in Hawaii. Environmental Fate There are a variety of microorganisms in soil, freshwater and marine ecosystems which are capable of degrading 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 process 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 containing 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, 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 demonstrated 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. Exposure may also occur through ingestion of contaminated food products and drinking water. 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.: 138ø C B.P.: 160ø C Vapor Pressure: 53 Pa at 160ø C Octanol/Water Partition (Kow): Log Kow = 2.81 Density/Spec. Grav.: 1.42 at 15ø C Solubility: 0.5 g/L of water at 20ø 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 Bioconcentration 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 10-8 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, Pennamine D, Plantgard, Tributon, Weed-B-Gon, 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 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 Toxic Release Inventory - Releases to Water and Land, 1987 to 1993 (in pounds): Water Land TOTALS 3,444 113,358 Top Five States HI 0 73,679 FL 5 38,456 MO 1,817 0 MI 822 8 TX 800 0 Major Industries Cane sugar 0 99,886 Agri. chems. 2,616 815 Plastics, resins 696 0 Misc. manufact. 0 400 Gen. Chemical 126 8 * Water/Land totals only include facilities with releases greater than a certain amount - usually 1000 to 10,000 lbs. For Additional Information: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: DALAPON 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 Health Effects Summary Acute: EPA has found dalapon to potentially cause the following health effects from acute exposures at levels above the MCL: no effects, but readily absorbed into and widely distributed throughout the body. Drinking water levels which are considered "safe" for short-term exposures: For a 10-kg (22 lb.) child consuming 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. Chronic: Dalapon has the potential to cause the following health effects from long-term exposures at levels above the MCL: increased kidney-to-body weight Cancer: There is inadequate evidence to state whether or not dalapon has the potential to cause cancer from lifetime exposure in drinking water. Usage Patterns Dalapon is a herbicide used to control grasses in a wide variety of crops, including fruit trees, beans, coffee, corn, cotton and peas. It is also registered for use in a number of non-crop applications such as lawns, drainage ditches, along railroad tracks, and in industrial areas. Dalapon is marketed as the sodium salt or as a mixture of the sodium and magnesium salts. Domestic production of dalapon in 1982 ranged between 7 and 9 million lbs. 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). Release Patterns Dalapon is released directly to the environment in its use as a herbicide for the control of annual and perennial grasses. Since dalapon is not a listed chemical in the Toxics Release Inventory, data on releases during its manufacture and handling are not available. Environmental Fate If released to soil, microbial degradation and leaching appear to be the important environmental fate processes. Dalapon leaches readily in soil; however, under conditions favorable for microbial growth, microbial degradation will probably proceed at a faster rate than leaching. In the absence of microbial action, dalapon degradation in soil is slow. The resultant average persistence of dalapon at recommended rates of application has been reported to be two to four weeks in most agricultural soils during the growing season, although a persistence of six months has been observed in soils of various forests and tree nurseries. If released to water, microbial degradation, hydrolysis, and photolysis are potentially important in the removal of 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. Atmospheric 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 for snails. BCF's of less than one have been measured for poultry, rodents, dogs, and cows. Occupational exposure to dalapon may occur through dermal and inhalation routes associated with the formulation and application of dalapon herbicide. Chemical/ Physical Properties CAS Number: 75-99-0 Color/ Form/Odor: Colorless liquid with an acrid odor; sold as sodium or magnesium salt M.P.: 20ø C B.P.: 190ø C Vapor Pressure: N/A Octanol/Water Partition (Kow): Log Kow = 0.778 Density/Spec. Grav.: 1.4 at 15ø C Solubility: 800 g/L of water at 25ø C; Very soluble in water Soil sorption coefficient: Koc N/A; very high mobility in soil Odor/Taste Thresholds: N/A Bioconcentration Factor: BCF =1 to 3; not expected to bioconcentrate 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 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: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: DIBROMOCHLOROPROPANE (DBCP) Drinking Water Standards MCLG: zero mg/L MCL: 0.0002 mg/L HAL(child): 1 day: 0.2 mg/L; 10-day: 0.05 mg/L Health Effects Summary Acute: EPA has found DBCP to potentially cause kidney and liver damage and atrophy of the testes. Drinking water levels which are considered "safe" for short-term exposures: For a 10-kg (22 lb.) child consuming 1 liter of water per day, a one-day exposure of 0.2 mg/L or a ten-day exposure to 0.05 mg/L. Chronic: DBCP has the potential to cause kidney damage and antifertility effects from long-term exposure at levels above the MCL. Cancer: There is some evidence that DBCP may have the potential to cause cancer from a lifetime exposure at levels above the MCL. Usage Patterns DBCP was once used as an unclassified nematocide for soil fumigation of cucumbers, summer squash, cabbage, cauliflower, carrots, snap beans, okra, aster, shasta daisy, ornamental turf (lawns), bermudagrass, centipedegrass, St Augustine grass, zoysia grass, ardisia, azalea, camellia, forsythia, gardenia, hibiscus, roses, and arborvitae. Though it is also used as a chemical intermediate in the production of a flame-retardant, essentially all of its present use is as a soil fumigant. Release Patterns In the past, release of DBCP to the environment occurred primarily from its fumigant and nematocide uses. In 1977, 831,000 pounds of DBCP was used in CA alone, mainly on grapes and tomatoes. In 1974, USA farmers applied 9.8 million pounds of DBCP on crops. All registrations of end use products were cancelled in 1979 except for the use as a soil fumigant against nematodes on pineapples in Hawaii. This use was cancelled in 1985. The use of DBCP as a laboratory reactant is not expected to result in significant release to the environment. Environmental Fate DBCP released to soil will likely volatilize or leach to groundwater. In a model soil assumed to contain 1,2-dibromo-3-chloropropane (DBCP) evenly distributed within the first 10 cm, the volatilization half-life of DBCP was estimated to be 1.2 days. The observed log soil sorption coefficient (Koc) of DBCP is 2.11 in an unspecified soil. In a soil containing 10% moisture, the log Koc of DBCP is 1.6. Modelling predicted that DBCP will adsorb so weakly that it will co-migrate with water through low organic content soil. In alkaline soils, hydrolysis may be significant and biodegradation is possible but is expected to be slow 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. Chemical/ Physical Properties CAS Number: 96-12-8 Color/ Form/Odor: Dense yellow liquid with pungent odor; may also be granular M.P.: 5ø C B.P.: 196ø C Vapor Pressure: 0.8 mm Hg at 21ø C Density/Spec. Grav.: 2.08 at 20ø C Octanol/Water Partition (Kow): Log Kow = 2.43 (calculated) Solubility: 1.23 g/L of water at 25ø C; Slightly soluble in water Soil sorption coefficient: Log Koc = 2.01; high mobility Odor/Taste Thresholds: Taste threshold in water is 0.01 mg/L Bioconcentration Factor: 11 (est.); low bioconcentration potential Henry's Law Coefficient: 1.47x10-4 atm-cu m/mole; Trade Names/Synonyms: DBCP; BBC 12; Fumagon; Fumazone; Nemabrom; Nemafum; Nemagon; Nemanax; Nemapaz; Nemaset; Nemazon; Gro-Tone Nematode; Durham Nematocide EM 17.1 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: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: DINOSEB 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: For a 10-kg (22 lb.) child consuming 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-harvest dessication of hops, leguminous seed crops, potatoes and for control of runners and suckers in strawberries and raspberries. Dinoseb is also used as a corn yield enhancer and an insecticide and miticide. 1982 production of dinoseb was reported as 6.2 million lbs., with consumption estimates as follows: as an herbicide 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 manufacture 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 dinoseb 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-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 constant of 5.04X10-4 atm cu m/mol suggests that volatilization of dinoseb from water will be slow. It is unlikely to undergo significant biodegradation in most natural waters. 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 deposition 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. Chemical/ Physical Properties CAS Number: 88-85-7 Color/ Form/Odor: Yellow/orange crystals; pungent odor M.P.: 38-42ø C B.P.: N/A Vapor Pressure: 1 mm Hg at 151.1ø C Octanol/Water Partition (Kow): N/A Density/Spec. Grav.: 1.26 at 45ø C Solubility: 0.052 g/L of water at 25ø 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 Bioconcentration Factor: BCF = 68 (est.); not expected to bioconcentrate in aquatic organisms. Henry's Law Coefficient: 5.04x10-4 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; Hel-fire; Caldon; Kiloseb; Sinox General; Subitex. 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: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: DIOXIN (2,3,7,8-TCDD) 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: For a 10-kg (22 lb.) child consuming 1 liter of water per day, a one-day exposure of 1x10-6 mg/L or a ten-day exposure to 1x10-7 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 chlorinated 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 polyesters 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 available. 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 sediments 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 water depth increases. Many bottom sediments may therefore not be susceptible to significant photodegradation. 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 demonstrated that TCDD is generally resistant to biodegradation. 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 contaminated 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 biodegradation. If released to the atmosphere, vapor-phase TCDD may be degraded by reaction with hydroxyl radicals and direct photolysis. Particulate-phase TCDD may be physically removed from air by wet and dry deposition. Bioconcentration in aquatic organisms has been demonstrated. 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 for various aquatic organisms: snails, fish (Gambusia), daphnia 4.3-4.4; duckweed, algae, catfish, 3.6-3.95. The major route of exposure to the general population results from incineration processes and exhausts from leaded gasoline engines. Chemical/ Physical Properties CAS Number: 1746-01-6 Color/ Form/Odor: White crystalline needles M.P.: 305-306ø C B.P.: N/A Vapor Pressure: 7.4x10-4 mm Hg, 25ø C Density/Spec. Grav.: N/A Octanol/Water Partition (Kow): Log Kow = 6.8 Solubility: 19.3 ng/L of water at 25ø C; Insoluble in water Soil sorption coefficient: Koc-N/A; very low mobility in soil Odor/Taste Thresholds: N/A Bioconcentration Factor: 3.2 to 3.9 in fish; expected to bioconcentrate 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; 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 Analysis: Reference Source Method Numbers EPA 821-B-94-005 1613 Treatment- Best Available Technologies: Granular Activated Charcoal For Additional Information: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 National Primary Drinking Water Regulations Technical Factsheet on: DIQUAT Drinking Water Standards MCLG: 0.02 mg/L MCL: 0.02 mg/L HAL(child): 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 following 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 destruction; 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 1980 was estimated to be 200,000 lbs. of active ingredient. 1982 data indicates that diquat was not produced domestically, but imports were nearly 835,000 lbs. 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, aquatic 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 manufacture 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 montorillonite clay, adsorption is considered irreversible. There is some evidence of a more loosely bound component, the fraction of which depends on the type of soil. Diquat is removed rapidly from aquatic systems, principally 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 spraying operations, it would be associated with aerosols. 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 partition 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. Chemical/ Physical Properties CAS Number: 85-00-7 Color/ Form/Odor: Colorless to yellow crystals; water solution is dark reddish brown M.P.: 335-340ø C B.P.: N/A Vapor Pressure: 1.3x10-5 mm Hg at 20ø C Octanol/Water Partition (Kow): Log Kow = -3.05 Density/Spec. Grav.: 1.22 - 1.27 at 20ø C Solubility: 700 g/L of water at 20ø 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 bioconcentrate 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 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 > 0.0004 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: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: ENDOTHALL Drinking Water Standards MCLG: 0.1 mg/L MCL: 0.1 mg/L HAL(child): 1- to 10-day: 0.8 mg/L; Longer-term: 0.2 mg/L Health Effects Summary Acute: EPA has found endothall to potentially cause the following health effects from acute exposures at levels above the MCL: depressed breathing and heart rate. Drinking water levels which are considered "safe" for short-term exposures: For a 10-kg (22 lb.) child consuming 1 liter of water per day, upto a ten-day exposure to 0.8, or up to a 7-year exposure to 0.2 mg/L. Chronic: Endothall has the potential to cause the following health effects from long-term exposures at levels above the MCL: increased organ weights and organ-to-body weight ratios of stomach and intestine. Cancer: There is inadequate evidence to state whether or not endothall has the potential to cause cancer from a lifetime exposure in drinking water. Usage Patterns Endothall is used as a defoliant for a wide range of crops and as a herbicide for both terrestrial and aquatic weeds. It is used as a desiccant on lucerne and on potato, for the defoliation of cotton, to control aquatic weeds and as an aquatic algicide growth regulator. It has been used for: sugar beets, turf, hops sucker suppression; alfalfa, clover desiccants; potato vine killers. EPA estimated total domestic usage in 1982 to have been approximately 1.5 million lbs. In California in 1984, 87,000 lbs. of the mono(N,N-diethylalkylamine) salt were used; 4,000 lbs. of the dimethylamine salt were used; minor amounts of the dimethylalkylamine and dipotassium salts were used. Its estimated applications in California were as follows: Cotton production, 95.6%; Sugarbeets, 3.9%; Remainder in landscape maintenance or "public health pest control." Release Patterns Release of endothall to the environment is expected to occur primarily during its use as a pre-emergence, post-emergence, turf and aquatic herbicide and harvest aid. Other sources of release include loss during manufacturing, formulation, packaging or disposal of this herbicide. Since endothall is not a listed chemical in the Toxics Release Inventory, data on releases during its manufacture and handling are not available. Environmental Fate If released to soil, endothall is expected to rapidly biodegrade under aerobic conditions. The half-life of endothall in soil is reported to be 4 to 9 days. Endothall should be highly mobile in soil; however, rapid degradation would limit the extent of leaching. Its persistence in soil may be prolonged by adsorption to organic matter or by factors inhibiting microbial activity. Chemical hydrolysis and volatilization are not expected to be significant. If released to water, endothall should rapidly biodegrade under aerobic conditions (half-life approximately 1 week or less) and biodegrade more slowly under anaerobic conditions. Glutamic acid is a major biotransformation product of endothall under aerobic conditions. Endothall is not expected to oxidize, chemically hydrolyze, photolyze, volatilize or adsorb to suspended solids or sediments in water. The soil adsorption coefficient (Koc) of endothall in sediment/water systems has been measured to be < 2. If released to the atmosphere, endothall is expected to 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 endothall in bluegill (Lepomis macrochirus) has been measured 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 endothall are inhalation and dermal contact of workers involved in the manufacture, handling or application of endothall. The general public could potentially be exposed through use for lawn weed control. Chemical/ Physical Properties CAS Number: 145-73-3 Color/ Form/Odor: Odorless, white crystals M.P.: 144ø C (decomposes) Vapor Pressure: very low at room temp. Octanol/Water Partition (Kow): N/A Density/Spec. Grav.: 1.431 at 15ø C Solubility: 100 g/L of water at 20ø C; Very soluble in water Soil sorption coefficient: Koc <2; high mobility in soil Odor/Taste Thresholds: N/A Henry's Law Coefficient: N/A Bioconcentration Factor: BCF <1 in fish; not expected to bioconcentrate in aquatic organisms. Trade Names/Synonyms: Hexahydro-3,6-endo-epoxy-1,2-benzenedicarboxylic acid; Accelerate; Aquathol; Des-i-cate; Endothall Turf Herbicide; Endothall Weed Killer; Herbicide 273; Hydrothol; Herbon Pennout; Hydout. 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: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: ENDRIN 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 confusion, convulsions. Drinking water levels which are considered "safe" for short-term exposures: For a 10-kg (22 lb.) child consuming 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 lbs. 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 buildings 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 photodegrade to 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. However, 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 particle-associated endrin to water systems Endrin released to water systems will not hydrolyze or biodegrade. It will be subject to photoisomerization to ketoendrin. It will extensively sorb to sediment. Evaporation from water will not be significant. Fate of endrin in the atmosphere is unknown, but it probably will be primarily associated with particulate matter and be removed mainly by rainout and dry deposition. 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. Chemical/ Physical Properties CAS Number: 72-20-8 Color/ Form/Odor: Odorless white crystals M.P.: 200ø C B.P.: decomp. 245ø C Vapor Pressure: 2x10-7 mm Hg at 25ø C Octanol/Water Partition (Kow): Log Kow = 5.6(calc.) Density/Spec. Grav.: 1.7 at 20ø 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 Bioconcentration 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; Compound 269; Hexachloroepoxy- octahydro-endo,endo-dimethano- naphthalene 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 600/4-88-039 505; 508; 508.1; 525.2 Treatment- Best Available Technologies: Granular Activated Charcoal For Additional Information: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: ETHYLENE DIBROMIDE (EDB) 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 ethylene dibromide (EDB) to potentially cause a variety of acute health effects, including damage to the liver, stomach, and adrenal cortex along with significant reproductive system toxicity, particularly the testes. Drinking water levels which are considered "safe" for short-term exposures: For a 10-kg (22 lb.) child consuming 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, insecticide, 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 associated 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 which have recently been restricted 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 Inventory EDB releases to land totalled 2,670 lbs., and water releases totalled 2,554 lbs. 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 moderate 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 radicals (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 volatilization does not occur, ethylene bromide can be degraded by biodegradation and hydrolysis. Uncatalyzed hydrolysis 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 photolyze 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 pertaining to ethylene bromide concluded that ethylene bromide is biotransformed fairly readily in the environment; lifetimes 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. Chemical/ Physical Properties CAS Number: 106-93-4 Color/ Form/Odor: Colorless, heavy liquid; mildly sweet chloroform-like odor. M.P.: 9.8ø C B.P.: 131-132ø 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 25ø 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; Iscobrome-D; Nefis; Pestmaster; EDB-85; Soilbrom; Soilfume; Kopfume 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 Toxic Release Inventory - Releases to Water and Land, 1987 to 1993 (in pounds): Water Land TOTALS 2,554 2,670 Top Six States CA 344 500 MS 342 500 HI 750 0 NJ 0 700 TX 110 466 PR 500 0 Top Industrial Sources Petroleum refining 2,119 1,716 Industrial organic 355 700 chemicals, fertilizers For Additional Information: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: GLYPHOSATE Drinking Water Standards MCLG: 0.7 mg/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: For a 10-kg (22 lb.) child consuming 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. Usage Patterns Glyphosate is a non-selective herbicide registered for use on many food and non-food crops as well as non-crop areas where total vegetation control is desired. When applied at lower rates, it serves as a plant growth regulator. The most common uses include control of broadleaf weeds and grasses in : hay/pasture, soybeans, field corn; ornamentals, lawns, turf, forest plantings, 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 eleventh among conventional pesticides in the US during 1990-91. In recent years, 13 to 20 million acres were treated with 18.7 million lbs. 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. Environmental Fate Glyphosate is most often applied as a spray of the isopropylamine salt and is removed from the atmosphere by gravitational settling. After glyphosate is applied to forests, fields, and other land by spraying, it is strongly adsorbed to soil, remains in the upper soil layers, and has a low propensity for leaching. Iron and aluminum clays and organic matter adsorbed more glyphosate than 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 accidental 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 expected 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. Chemical/ Physical Properties CAS Number: 1071-83-6 Color/ Form/Odor: Odorless white crystals M.P.: 230ø C B.P.: N/A Vapor Pressure: Negligible Octanol/Water Partition (Kow): N/A Density/Spec. Grav.: 0.5g/ml at 15ø C Solubility: 12 g/L of water at 25ø C; Soluble in water Soil sorption coefficient: Strong, reversible adsorption Odor/Taste Thresholds: N/A Henry's Law Coefficient: N/A Bioconcentration Factor: BCF <1 in fish; not expected to bioconcentrate in aquatic organisms. Trade Names/Synonyms: N-(phosphonomethyl) glycine; Glialka; Roundup; Sting; Rodeo; Spasor; Muster; Tumbleweed; Sonic; Glifonox; Glycel; Rondo 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: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: HEPTACHLOR AND HEPTACHLOR EPOXIDE Drinking Water Standards (in mg/L) MCLG MCL HAL(1day) Heptachlor: zero 0.0004 0.01 - epoxide: zero 0.0002 0.01 Health Effects Summary Acute: EPA has found heptachlor to potentially cause liver and central nervous system damage from short-term exposures at levels above the MCL. Short-term exposures in drinking water which are considered "safe" for a 10-kg (22 lb.) child consuming 1 liter of water per day: a one- to ten-day exposure to 0.01 mg/L. Chronic: Heptachlor and its epoxide have the potential to cause extensive liver damage from long-term exposure at levels above the MCL. Cancer: There is some evidence that both heptachlor and heptachlor epoxide have the potential to cause cancer from a lifetime exposure at levels above the MCL. Usage Patterns Production of heptachlor in 1982 was nearly 100,000 lbs, all of which was used as a non-agricultural insecticide. Most uses of the product were cancelled in 1978. The only permitted commercial use of heptachlor products is for fire ant control in buried, pad-mounted electric power transformers, and in underground cable television and telephone cable boxes. Release Patterns Heptachlor may be released directly to the soil in connection with its use in termite and fire ant control. However, heptachlor has been found in treated wastewater from some types of industrial facilities. Based on monitoring data, mean loadings in various wastestreams are: coal mining - 0.0081, foundries - 0.030 and nonferrous metals manufacturing - 0.0008. Heptachlor epoxide is not produced commercially, but rather is formed by the chemical and biological transformation of heptachlor in the environment. Environmental Fate Release of heptachlor to soil surfaces will result in volatilization from the surface, especially in moist soils, but volatilization of heptachlor incorporated into soil will be slower. Hydrolysis in moist soils is expected to be significant. In soil, heptachlor will degrade to 1-hydroxychlordene, heptachlor epoxide and an unidentified metabolite less hydrophilic than heptachlor epoxide. Biodegradation may also be significant. Heptachlor is expected to adsorb strongly to soil and, therefore, to resist leaching to groundwater. Heptachlor epoxide adsorbs strongly to soil and is extremely resistant to biodegradation, persisting for many years in the upper soil layers. Some volatilization or photolysis loss may occur. Release of heptachlor to water will result in hydrolysis to 1-hydroxychlordene (half-life of about 1 day) and volatilization. Adsorption to sediments may occur. Biodegradation of heptachlor may occur, but is expected to be slow compared to hydrolysis. Direct and photosensitized 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 photochemically generated hydroxyl radicals with an estimated 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 radical 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 various fish species. Bioconcentration may be limited, however, by the rapidity of heptachlor hydrolysis in water and the adsorption of heptachlor to sediments. Heptachlor epoxide is bioconcentrated extensively. It is taken up into the food chain by plants and bioconcentrates into fish, animals and milk. Heptachlor and Heptachlor Epoxide Chemical/ Physical Properties CAS Number: Heptachlor- 76-44-8; Heptachlor epoxide- 1024-57-3 Color/ Form/Odor: White to light tan waxy solid with a camphor-like odor. Available as emulsifiable concentrates and oil solutions. The epoxide is formed from heptachlor in the environment. M.P.: 95-96ø C B.P.: 145ø C Octanol/Water Partition (Kow): Log Kow = 3.9 to 5.4 (est.) Density/Spec. Grav.: 1.57 at 9ø C Solubility: 0.03 mg/L of water at 25ø C; insoluble in water Vapor Pressure: 3x10-4 mm Hg at 25ø C Soil sorption coefficient: Log Koc estimated at 4.48; low to very low mobility in soil Odor/Taste Thresholds: N/A Bioconcentration Factor: 5000 to 15,000 in fish; potential to bioconcentrate in aquatic organisms. Henry's Law Coefficient: 2.62x10-3 atm-cu m/mole; Trade Names/Synonyms: 3-Chlorochlordene; Aahepta; Agroceres, Hepta, Heptachlordane, Heptagran, Heptamul, Heptox, Gold Crest H-60, Rhodiachlor, Velsicol 104, Basaklor, Soleptax, Termide 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: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: HEXACHLOROBENZENE (HCB) 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 hexachlorobenzene (HCB) 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 lb.) child consuming 1 liter of water per day, upto a 7-year exposure to 0.05 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 tetrachloroethylene, 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 lbs, with no evidence of commercial domestic production. However, 2 to 5 million lbs may be generated each year as a waste by-product of chlorination processes in chemical manufacture. 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 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 Chemical Release Inventory, HCB releases to land and water totalled 1,287 lbs., all of which was to water. These releases were primarily from alkali, chlorine and agricultural 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 biodegradation 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, contaminated drinking water and food, as well as contact with contaminated soil or occupational atmospheres. Chemical/ Physical Properties CAS Number: 118-74-1 Color/ Form/Odor: White needles M.P.: 231ø C B.P.: 323-326ø C Vapor Pressure: 1.09x10-5 mm Hg, 25ø C Octanol/Water Partition (Kow): Log Kow = 5.31 Density/Spec. Grav.: 1.57 at 23.6ø C Solubility: 0.035 mg/L of water; Insoluble 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 organisms. 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, Pentachlorophenyl chloride, Anticarie, Bunt-cure, Co-op hexa, Julin's carbon chloride, No bunt 40, No bunt 80, Sanocide, Snieciotox, Smut-go, Granox nm, Voronit C 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 600/4-88-039 505; 508; 508.1; 525.2 Treatment- Best Available Technologies: Granular Activated Charcoal Toxic Release Inventory - Releases to Water and Land, 1987 to 1993 (in pounds): Water Land TOTALS 1,286 1 Top States LA 677 1 TX 609 0 Major Industries Alkalies, chlorine 854 1 Agricultural chemicals 297 0 For Additional Information: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: HEXACHLOROCYCLOPENTADIENE (HEX) Drinking Water Standards MCLG: 0.05 mg/L MCL: 0.05 mg/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: gastrointestinal 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 lbs. of HEX are produced each year. Its greatest use is as an intermediate in chemical manufacture, including the synthesis of chlorinated pesticides, flame retardants, resins, dyes, pharmaceuticals, plastics, etc. HEX has no end uses of its own. Release Patterns Major sources 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 incineration of certain chlorinated wastes, and from water treatment plants receiving contaminated wastestreams. From 1987 to 1993, according to EPA's Toxic Chemical Release Inventory, HEX releases to land and water totalled only 78 lbs., all of which was to water. These releases were primarily from alkalis and chlorine industries. The largest releases occurred in New York. Environmental Fate Hexachlorocyclopentadiene is not a persistent environmental 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 several weeks. Biodegradation is expected to be of minor importance. Hexachlorocyclopentadiene could potentially bioaccumulate in some aquatic organisms depending upon the species. Bioconcentration factors of hexachlorocyclopentadiene in a laboratory model ecosystem: alga, 341; snail, 929; mosquito, 1634; and fish, 448. Chemical/ Physical Properties CAS Number: 77-47-4 Color/ Form/Odor: dense, oily, yellow green liquid with a pungent odor. M.P.: -9ø C B.P.: 239ø C Vapor Pressure: 0.08 mm Hg at 25ø C Octanol/Water Partition (Kow): Log Kow = 3.99 Density/Spec. Grav.: 1.7 at 25ø C Solubility: 2 m/L of water at 25ø C; Insoluble in water Soil sorption coefficient: Koc measured at 4,265; low mobility in soil Odor/Taste Thresholds: N/A Bioconcentration 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 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 600/4-88-039 505; 508; 508.1; 525.2 Treatment- Best Available Technologies: Granular Activated Charcoal For Additional Information: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: LINDANE Drinking Water Standards MCLG: 0.0002 mg/L MCL: 0.0002 mg/L HAL(child): 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 pulmonary edema have been reported in children with acute exposures. Drinking water levels which are considered "safe" for short-term exposures: For a 10-kg (22 lb.) child consuming 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 manufacturing - 0.0004. From 1987 to 1993, according to EPA's Toxics Release Inventory, lindane releases to land and water totalled 1115 lbs. Environmental Fate When released to water, lindane is not expected to volatilize significantly. The volatilization half-life of lindane 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. Lindane 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. 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 groundwater Lindane in the atmosphere is likely to be subject to rain-out and dry deposition. The estimated half-life for the reaction of vapor phase lindane with atmospheric hydroxyl radicals is 1.63 days. Lindane will bioconcentrate slightly in fish. Bioconcentration factors of 16 to 1600 are reported for a variety of molluscs, crustaceans and fish. Chemical/ Physical Properties CAS Number: 58-89-9 Color/ Form/Odor: White crystalline solid M.P.: 112.5ø C B.P.: 323.4ø C Vapor Pressure: 9.4x10-6 mm Hg @ 25ø C Density/Spec. Grav.: 1.85 Octanol/Water Partition (Kow): Log Kow = 3.72 to 3.61 Solubility: 7.3 mg/L of water at 25ø C; Slightly soluble in water Soil sorption coefficient: average Koc = 1081; low soil mobility Odor/Taste Thresholds: N/A Bioconcentration 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, Lindagranox, Lindaterra, Lovigram, Silvanol 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 600/4-88-039 505; 508; 508.1; 525.2 Treatment- Best Available Technologies: Granular Activated Charcoal For Additional Information: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: METHOXYCHLOR 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 lb.) child consuming 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. Usage Patterns Methoxychlor is preferred to DDT for use on animals, in animal feed, and on DDT-sensitive crops such as squash, melons, etc. Since methoxychlor is more unstable than DDT, it has less residual effect. Compared to DDT, methoxychlor, is more toxic to some insects & less toxic to 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 methoxychlor has decreased: from 3.7 million lbs. in 1978 to 700,000 lbs in 1982. In 1982 it was estimated that industries consumed methoxychlor as follows: 43 percent as an insecticide for livestock and poultry, 29 percent 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, deciduous fruits and nuts, and vegetables Other sources of release may include loss during the manufacture, formulation, packaging, and disposal of methoxychlor. From 1987 to 1993, according to EPA's Toxic Chemical Release Inventory, methoxychlor releases to land and water totalled only about 2000 lbs. Environmental Fate Methoxychlor does not tend to persist when released to soil or water, and does not accumulate in fish. If released to soil, methoxychlor is expected to remain immobilized primarily in the upper layer of soil although a small percentage may migrate to lower depths, possibly into groundwater as suggested by the detection of methoxychlor 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, biodegradation 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. Methoxychlor 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) depending upon the presence of photosensitizers. Based on the Henry's law constant, volatilization of methoxychlor 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 hydroxyl 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 methoxychlor fairly rapidly 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. Chemical/ Physical Properties CAS Number: 72-43-5 Color/ Form/Odor: Colorless crystals with slightly fruity odor; available as: wettable powder; emulsifiable, dust and aerosol concentrates; oil solutions M.P.: 89 ø C B.P.: N/A Vapor Pressure: very low Density/Spec. Grav.: 1.41 at 25ø C Octanol/Water Partition (Kow): Log Kow = 4.83, 4.91 and 5.08 Solubility: 0.10 mg/L of water at 25ø C; Slightly soluble in water Henry's Law Coefficient: 1.6x10-5 atm-cu m/mole at 25ø C Odor/Taste Thresholds: odor threshold is 4.7 mg/L in water Soil sorption coefficient: measured Koc ranges from 9700 to 41,000 in sand to 80,000 to 100,000 in fine silt; low mobility in soil Bioconcentration Factor: BCFs 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-methoxyphenyl)-1,1,1-trichloroethane, dianisyl trichloroethane, Dimethoxy-DDT, Methoxy-DDT, Chemform, Maralate, Methoxo, Methoxcide, Metox, Moxie 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 600/4-88-039 505; 508; 508.1; 525.2 Treatment- Best Available Technologies: Granular Activated Charcoal For Additional Information: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: OXAMYL Drinking Water Standards MCLG: 0.2 mg/L MCL: 0.2 mg/L HAL(child): 1- 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 MCL: tremors, salivation and tearing due to cholinesterase inhibition. Drinking water levels which are considered "safe" for short-term exposures: For a 10-kg (22 lb.) child consuming 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 lbs. of oxamyl were produced in the US in 1982. Release Patterns Oxamyl is released directly to the environment in its use as an insecticide and during its manufacture, handling and storage. Since oxamyl is not a listed chemical in the Toxics Release Inventory, data on releases during its manufacture and handling are not available. Environmental Fate Oxamyl is highly soluble in water, and is relatively stable in aqueous solutions at acidic pH. It hydrolyzes 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 biodegradation. 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. Chemical/ Physical Properties CAS Number: 23135-22-0 Color/ Form/Odor: White crystals with slight sulfurous odor. M.P.: 100-192ø C, different crystalline form at 108-110ø C Vapor Pressure: N/A Octanol/Water Partition (Kow): N/A Density/Spec. Grav.: N/A Solubility: 280 g/L of water at 25ø C; Very soluble in water Soil sorption coefficient: N/A Odor/Taste Thresholds: N/A Bioconcentration Factor: N/A Henry's Law Coefficient: N/A Trade Names/Synonyms: Vydate K; Thioxamyl; Dioxamyl; DPX 1410; Dupont 1410; Methyl N',N'-dimethyl-N-((methylcarbamoyl)oxy)- 1-thiooxamimidate 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 > 0.002 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: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: PENTACHLOROPHENOL Drinking Water Standards MCLG: zero mg/L MCL: 0.001 mg/L HAL(child): 1 day: 1 mg/L; Longer-term: 0.3 mg/L Health Effects Summary Acute: EPA has found pentachlorophenol to potentially 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 lb.) child consuming 1 liter of water per day, an 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 pentachlorophenol 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 treating agent for beans; antibacterial agent in disinfectants/cleaners; preharvest defoliant on some crops; preservative for glues, starches, photographic papers. Production of pentachlorophenol was 45 million lbs in 1983. In 1983 it was estimated that industries consumed PCP as follows: Wood Preservative, 90%; Sodium Pentachlorophenate, 10% Release Patterns Pentachlorophenol may be released to the environment as a result of its manufacture, storage, transport, or use as an industrial wood preservative for utility poles, cross arms, and fenceposts, and other items that consumes 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 Chemical Release Inventory, pentachlorophenol releases to land and water totalled nearly 100,000 lbs., 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 slow biodegradation and leaching into groundwater. Pentachlorophenol 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 approximately weeks to months. In an artificial stream, microbial degradation became significant after 3 weeks and accounted for 26-46% removal. Pentachlorophenol mineralization 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 unsaturated 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 moderate vapor pressure would suggest that evaporation from water is not rapid, especially at natural pHs where pentachlorophenol 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 previous year), which was inversely dependent on the concentration of pentachlorophenol and microbial biomass. Pentachlorophenol does not appear to oxidize or hydrolyze under environmental conditions; however, photolysis 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. Pentachlorophenol is expected to bioconcentrate because of its low water solubility, but the bioconcentration factor will be dependent upon the pH of the water since pentachlorophenol 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 mosquito fish; 2.85 in zebra fish; 2.62 in golden orfe. 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 pentachlorophenol via inhalation and dermal contact primarily in situations where they use this preservative or are in contact with treated wood product. The general population will be exposed primarily from ingesting food contaminated with 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.: 190-191ø C B.P.: 309-310ø C Vapor Pressure: 0.00011mm Hg at 25ø C Density/Spec. Grav.: 1.98 at 22ø C Octanol/Water Partition: Log Kow= 5.12 Solubility: 0.02 g/L of water at 30ø C; 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, Ortho Triox, Osmose WPC, Watershed WP, Weed and Brush Killer 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 Analysis: Reference Source Method Numbers EPA 600/4-88-039 515.1; 515.2; 525.2; 555 Treatment- Best Available Technologies: Granular Activated Charcoal Toxic Release Inventory - Releases to Water and Land, 1987 to 1993 (in pounds): Water Land TOTALS 18,700 79,780 Top Five States NV 0 64,100 OR 4,313 5,405 WA 3,310 5,995 AR 2,735 1,615 GA 783 1,255 Major Industries Explosives 0 34,100 Wood preserving 17,720 15,678 Misc. Chemicals 250 30,000 * Water/Land totals only include facilities with releases greater than a certain amount - usually 1000 to 10,000 lbs. For Additional Information: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: DI (2-ETHYLHEXYL) PHTHALATE (DEHP) 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, decorative 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 lbs in 1982 to over 286 million lbs. in 1986, with imports of 6 million lbs. In 1986, it was estimated that industries consumed DEHP as follows: plasticizer for polyvinyl chloride, 95%; other uses, 5%. Release Patterns DEHP is used in large quantities, primarily as a plasticizer for polyvinyl chloride and other polymeric materials. Disposal of these products (incineration, landfill, etc) will result in the release of DEHP into the environment. DEHP has been detected in the effluent of numerous industrial plants. From 1987 to 1993, according to EPA's Toxic Chemical Release Inventory, DEHP releases to land and water totalled over 500,000 lbs., 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 demonstrates 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 acclimation. 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. Chemical/ Physical Properties CAS Number: 117-81-7 Color/ Form/Odor: Colorless oily liquid M.P.: -50ø C B.P.: 230ø C (5 mm Hg) Vapor Pressure: 1.32 mm Hg at 200ø C Octanol/Water Partition (Kow): Log Kow = 4.89 Density/Spec. Grav.: 0.99 at 20ø C Solubility: 0.285 mg/L of water at 24ø C; Slightly soluble in water Soil sorption coefficient: Log Koc measured at 4 to 5; low mobility in soil Odor/Taste Thresholds: N/A Bioconcentration Factor: Log BCF =2 to 4 in fish; expected to bioconcentrate in aquatic organisms. Henry's Law Coefficient: 1x10-4 atm-cu m/mole Trade Names/Synonyms: DEHP; Bis(2-ethylhexyl)-phthalate; BEHP; Dioctyl phthalate; Pittsburgh PX-138; Platinol AH; RC Plasticizer DOP; Reomol D79P; Sicol 150; Staflex DOP; Truflex DOP; Vestinol AH; Vinicizer 80; Palatinol AH; Hercoflex 260; Kodaflex DOP; Mollan O; Nuoplaz DOP; Octoil; Eviplast 80; Fleximel; Flexol DOP; Good-rite GP264; Hatcol DOP; Ergoplast FDO; DAF 68; Bisoflex 81 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 Toxic Release Inventory - Releases to Water and Land, 1987 to 1993 (in pounds): Water Land TOTALS* (in pounds) 16,910 471,191 Top Five States* WI 500 255,000 TN 3,491 80,419 OH 268 62,982 NJ 3,956 23,139 NY 500 13,284 Major Industries Misc rubber products 274 311,900 Rubber, plastic hose 10 80,019 Cyclic crudes, intermed. 3,099 12,200 * Water/Land totals only include facilities with releases greater than 100 lbs. For Additional Information: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 National Primary Drinking Water Regulations Technical Factsheet on: PICLORAM Drinking Water Standards MCLG: 0.5 mg/L MCL: 0.5 mg/L HAL(child): 1- to 10- day: 20 mg/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 system, weakness, diarrhea, weight loss. Drinking water levels which are considered "safe" for short-term exposures: For a 10-kg (22 lb.) child consuming 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-croplands 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 lbs. 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 production 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 chlorobenzoic acid herbicides. If picloram 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 amine, 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 evaporate 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 subject to degradation in surface waters. As an aromatic amine, its rate of degradation in water and soil may be 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. 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.: 218-219ø C B.P.: _ø C Vapor Pressure: 6.2x10-7 mm Hg, 25ø C Octanol/Water Partition (Kow): N/A Density/Spec. Grav.: N/A Solubility: 430 mg/L of water at 25ø C; Soluble in water Soil sorption coefficient: Koc average= 13; moderate mobility in soil Odor/Taste Thresholds: N/A Bioconcentration 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 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: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: POLYCHLORINATED BIPHENYLS (PCBs) 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 pigmentation 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; changes in liver function. Cancer: There is some evidence that PCBs may have the potential to cause cancer from a lifetime exposure at levels above the MCL. Usage Patterns Production of PCBs has decreased drastically: from over 86 million lbs. in 1970 to 35 million lbs 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 extenders, dedusting agents, pesticide extenders, inks, lubricants, cutting oils, in heat transfer systems, carbonless reproducing paper. 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 and then revolatilization. PCBs are also currently released to the environment from landfills containing PCB waste materials and products, incineration of municipal refuse and sewage sludge, and improper (or illegal) disposal of PCB materials, such as waste transformer fluid, to open areas. From 1987 to 1993, according to EPA's Toxic Chemical Release Inventory, PCB releases to land and water totalled over 74,000 lbs., 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 insulating 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 environmental fate mechanisms generally depends on the degree of chlorination. In general, the persistence of PCBs increases with an increase in the degree of chlorination. Mono-, di- and trichlorinated biphenyls biodegrade relatively rapidly, tetrachlorinated biphenyls biodegrade slowly, and higher chlorinated biphenyls are resistant to 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 chlorinated congeners will have a lower tendency 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 important fate mechanism with the rate of volatilization decreasing with increasing chlorination. Although the volatilization rate may be low, the total loss by volatilization over time may be significant because of the persistence and stability of PCBs. Enrichment of the low-Cl PCBs occurs in the vapor phase relative to the original Aroclor; the residue will be enriched in the PCBs containing high Cl content. If released to water, adsorption to sediment and suspended 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 (especially the higher chlorinated congeners) for relatively long 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 adsorption to sediment significantly competes with volatilization, 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 over time 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. The dominant atmospheric transformation process is probably the vapor-phase reaction with hydroxyl radicals which has estimated 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 chlorinated congeners. The major PCB exposure routes to humans are through food and drinking water, and by inhalation of contaminated air. 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 to 375ø 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 30ø 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 Bioconcentration 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, Kanechlor, Aroclor, Fenclor, Chlorextol, Dykanol, Inerteen, Monter, Pyralene, Santotherm, sovol, Therminol, Noflamol 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 Toxic Release Inventory - Releases to Water and Land, 1987 to 1993 (in pounds): Water Land TOTALS 784 73,632 Top Five States CA 0 58,178 NJ 0 13,188 KY 250 750 WA 0 998 TN 255 251 Major Industries Non-ferrous wire 0 58,178 Steel pipe/tubing 0 13,183 Pulp mills 0 998 For Additional Information: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 National Primary Drinking Water Regulations Technical Factsheet on: SIMAZINE 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 Acute: EPA has found simazine to potentially cause the following health effects from acute exposures at levels above the MCL: weight loss, changes in blood. Drinking water levels which are considered "safe" for short-term exposures: For a 10-kg (22 lb.) child consuming 1 liter of water per day, up to a 7-year exposure to 0.07 mg/L. Chronic: Simazine has the potential to cause the following health effects from long-term exposures at levels above the MCL: tremors; damage to testes, kidneys, liver and thyroid; gene mutations. Cancer: There is some evidence that simazine may have the potential to cause cancer from a lifetime exposure at levels above the MCL. Usage Patterns Simazine is a pre-emergence herbicide used for control of broad-leaved and grassy weeds on a variety of deep-rooted crops such as artichokes, asparagus, berry crops, broad beans, citrus, pome and stone fruits orchards, and others. It is also used on non-crop areas such as farm ponds, fish hatcheries, etc. Its major use is on corn where it is often combined with AAtrex. Other herbicides with which simazine is combined 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. Release Patterns Simazine may be released into the environment via effluents at manufacturing sites and at points of application where it is employed as a herbicide. Since simazine is not a listed chemical in the Toxics Release Inventory, data on releases during its manufacture and handling are not available. Environmental Fate If released to water, simazine is not expected to adsorb to sediment and suspended particulate matter, or to volatilize. Persistence depends upon many factors including degree of algae and weed infestation. Simazine residues may persist up to 3 years in soil under aquatic field conditions. Dissipation of simazine in pond and lake water was variable, with half-lives ranging from 50 to 700 days. Slow biodegradation of simazine may occur in water based upon the slow biodegradation observed in soil. Simazine is fairly resistant to hydrolysis. However, chemical hydrolysis of simazine may be more important environmentally than biodegradation at low pH or when various catalysts are present. 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 groundwater; 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 (purportedly mainly soil catalyzed hydrolysis) of simazine in two soil 45 and 100 days. Simazine can be utilized by certain soil microorganisms as a source of energy and mineralization. No degradation of simazine was detected in a soil suspension 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. Chemical/ Physical Properties CAS Number: 122-34-9 Color/ Form/Odor: White powder M.P.: 225ø C B.P.: N/A Vapor Pressure: 6.1x10-9 Octanol/Water Partition (Kow): Log Kow = 2.18 Density/Spec. Grav.: 1.3g/ml at 20ø C Solubility: 5 mg/L of water at 20ø C; Soluble in water Odor/Taste Thresholds: N/A Soil sorption coefficient: Koc =135 (measured); slight to high mobility in soil, depending upon other factors Henry's Law Coefficient: 4.63x10-10 atm-cu m/mole Bioconcentration Factor: 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; Herbazin; Herbex; Hungazin; Premazine; Primatol S; Pricep; Printop; Radocon; Simadex; Tafazine; Zeapur; 2-chloro-4,6-bis(ethylamino)-1,3,5-Triazine 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 Analysis: Reference Source Method Numbers EPA 600/4-88-039 505; 507; 508.1; 525.2 Treatment- Best Available Technologies: Granular Activated Charcoal For Additional Information: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: TOXAPHENE Drinking Water Standards MCLG: zero mg/L MCL: 0.003 mg/L HAL(child): none Health Effects Summary 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 considered "safe" for short-term exposures. Chronic: Toxaphene has the potential to cause the following health effects from long-term exposures at levels above the MCL: 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 & recommended 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 special local needs. Strobane T-90 has a broad spectrum activity as stomach & contact residual insecticide, & it has shown activity against several species of worms, scab, mites, hornflies, lice & mealybugs & major cotton insects. In the past, it has been used as piscicide (fish toxicant) in lakes. Other minor uses: for armyworms, cutworms, & grasshoppers; for mealybug & pineapple gummosis moth control on pineapples & weevil control on bananas. Conditional and restricted use as an insecticide and as a miticide in foliar treatment of: cranberries, strawberries, apples, pears, quinces, nectarines, peaches, bananas, pineapple, eggplant, peppers, pimentos, tomatoes, broccoli, brussel sprouts, cabbage, cauliflower, collards, kale, kohlrabi, spinach, lettuce (head and leaf), parsnips, rutabagas, 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, and noncrop areas. Also used in seed crop foliar treatment of clover and trefoil; in soil treatment of corn; in back rubber of beef cattle; in animal treatment of goats, sheep, beef cattle, and hogs; and aerial application and tank mixtures. Release Patterns Toxaphene is released into the environment primarily from its application as an insecticide for the protection of 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 removed by runoff. In water it will not appreciably hydrolyze, photolyze, or significantly biodegrade. It will strongly sorb to sediments. Little information concerning biodegradation of toxaphene 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 degradation 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 toxaphene. Anaerobic conditions in sediments led to nearly 50% overall degradation of 3 main components of toxaphene; 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 yr to 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 significant 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 important fate process (estimated half-life 4-5 days). Toxaphene can be transported long distances in the air (1200 km) probably adsorbed to particular matter. Bioconcentration factors (BCF) for fish - 3100 to 69,000; for shrimp 400-1200; Algae - 6902; snails - 9600. These BCF values indicated significant bioconcentration potential. Chickens fed 5, 50, or 100 ppm toxaphene in the diet, residues are detected in eggs and adipose tissue with a BCF of about 5. Monitoring data demonstrates that toxaphene is a contaminant in some air, water, sediment, soil, fish and other aquatic organisms, foods and birds. Human exposure appears to come mostly from food or occupational exposure. Chemical/ Physical Properties CAS Number: 8001-35-2 Color/ Form/Odor: Amber waxy solid with a piney odor; a mixture of polychlorinated compounds, available as a dust, wettable powder, or as emulsifiable or oil solutions M.P.: 65-90øC B.P.: Decomposes Vapor Pressure: 0.4 mm Hg at 25ø C Octanol/Water Partition (Kow): Log Kow = 3.3 Density/Spec. Grav.: 1.65 at 25ø C Solubility: 3 mg/L of water at 22ø C; Slightly soluble in water Soil sorption coefficient: Koc = 2.1x105; very low mobility in soil Odor/Taste Thresholds: Odor threshold 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, Geniphene, Hercules 3956, M5055, Melipax, Motox, Penphene, Phenacide, Phenatox, Strobane-T, Toxadust, Toxakil, Vertac 90%, Toxon 63, Attac, Anatox, 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 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 600/4-88-039 505; 508; 525.2 Treatment- Best Available Technologies: Granular Activated Charcoal For Additional Information: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378 National Primary Drinking Water Regulations Technical Factsheet on: 2,4,5 - TP Drinking Water Standards MCLG: 0.05 mg/L MCL: 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: For a 10-kg (22 lb.) child consuming 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 following health effects from long-term exposures at levels above the MCL: minor liver and kidney damage 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, 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 sugarcane, 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 application 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. Environmental Fate 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 from 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 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 dependent 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 operations 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 photooxidation 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 because all registered uses of silvex were canceled effective Jan 2, 1985. 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.: 181.6ø C B.P.: N/A Vapor Pressure: N/A Octanol/Water Partition (Kow): N/A Density/Spec. Grav.: 1.21 at 20ø C Solubility: 200 mg/L of water at 25ø 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 Bioconcentration Factor: BCF=58 in fish; not expected to bioconcentrate in aquatic organisms. Trade Names/Synonyms: 2,4,5-Trichlorophenoxyproprionic acid; Weed-B-Gon; Propon; Silvi-Rhap; Sta-fast; Miller Nu Set; Aqua-Vex; Color-Set; Ded-Weed; Fenoprop; Fenormone; Fruitone T; Garlon; Kuran; Kurosal G/SL; Silvex 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: EPA can provide further regulatory and other general information: ú EPA Safe Drinking Water Hotline - 800/426-4791 Other sources of toxicological and environmental fate data include: ú Toxic Substance Control Act Information Line - 202/554-1404 ú Toxics Release Inventory, National Library of Medicine - 301/496-6531 ú Agency for Toxic Substances and Disease Registry - 404/639-6000 ú National Pesticide Hotline - 800/858-7378