Document jNEXKqLxEXE5GoMynRNZR81BZ

A Division of The Sociei y of The Plastics Industry, Inc. August 13, 1990 (/cc TO: The Vinyl Insti tute Health, Safety and Environment Committee and The Vinyl Insti tute Technical, Medi cal Subcommittee RE: Dow's Comments cn California Air Resources Board Draft Document Through the courtesy of John Krokosky of Dow Chemical, I am pleased to enclose a copy of the comments filed by Dow in connection with the California Air Resources Board Draft Document on "Proposed Identification of Vi iyl Chloride as a Toxic Air Contaminant". I believe you will ::ind this a useful document relative to risk assessment methodolob;y relating to vinyl chloride emissions. cc: John Krokosky Dow Chemical RTG/bg SPI-00922 Wayne Interchange Plaza II 155 Route 46 West * Wayne, NJ 07470 (201) 890-9299 Fax ft (201) 890-7029 THE DOW CHEMICAL COMPANY MIDLAND MICHIGAN 48674 1803 BUILDING July 3,1990 Ms. Barbara Cook Project Manager California Air Resources Board 1102 Q Street Sacramento, CA 93814 fifCD AUG 13199Q Dear Ms. Cook: Attached are our co mments on the unit risk derivation presented in the May, 1990 Draft Technica. Support Document, Proposed Identification of Vinyl Chloride as a Toxic Air Contaminant. We appreciate your accepting our comments, which have been submitted to promote the best possible science in the performance of health risk assessments. Pleased call on us s lould you require additional information. Sincerely, V 'L., 'T 7 Neil C. Hawkins, Sc D. Senior Research Risk Analyst Health and Enviroiimental Sciences 1803 Building (517) 636-8237 kal Attachments SPI-00923 COMMENT: DRAFT TECHNICAL SUPPORT DOCUMENT, MAY, 1990, "PROPOSED IDENT1 FICATION OF VINYL CHLORIDE AS A TOXIC AIR CONTAMINANT" Derivation of a unit ri:k for Vinyl Chloride (CAS 75-01-4) VCM is clearly a rat md human carcinogen, causing liver angiosarcoma in both species and zym >al gland tumors in rats. Thus, for regulatory purposes, there is interest in deriving a quantitative estimate of a level of no significant risk. There are two general approaches to this problem. One approach has been the use of safety factors or uncertainty factors applied to no-observedeffect-levels (NOEL's) in animals to derive a safe level in humans. The other general approach, which has been used more recently by regulatory agencies, has been the use of quantitative risk assessment to estimate levels of risk for any given exposure The risk assessment process involves a number of decision points for w lich there is no scientific consensus as to the correct approach. These are: s of uncertainty, including the presence or absence of thresholds, the shap j of the dose response model, and animal to man conversion factors, have been resolved within the agencies through the use of policy decisions as to a default methodology. The default methodology is conservative in nature, so as to protect public health. However, the State of California Cancer Riik Assessment Guidelines as well as EPA and OSTP guidelines on the u ;e of risk assessment clearly state that the default methodology should iiot be used when other data are available. In particular, epidemiology data and pharmacokinetic information should be incorporated into risk assessment when the appropriate data are available. The DHS unit risk for vinyl chloride of 20 x 10(-5) per ppb, as cited in the CARB Draft Technical Document (CARB, 1990), does not utilize the available pharmacokinetic or epidemiological information. Pharmacokinetic Information Pharmacokinetic (PK) information can be used in two ways to augment risk assessments for vinyl chloride. PK data have been used to demonstrate and explain nonlinear bet..avior at both the high dose and low dose portions of the dose-response curve. The bioassay data of Maltoni (1979) clearly indicated a plateau in the dose-response curve at high doses. This phenomenon can be explained by the use of a Michaelis-Menton function to calculate metabolite concentrations, as suggested by Watanabe et al. (1976), and implemented by Gehring et al. (1978' Crump (1982) and USEPA (1987). However, this methodology only e<plains the high-dose results in the animal bioassay rather than addressin 5 the problem of low-dose extrapolation. Low-dose risk assessments utilizing 3K data have been discussed by Gehring et al. (1979) and Anderson et al. (1980 SPI-00924 -2- Purchase et al. (1980 reviewed risk assessments for VCM and showed that, among the linear micjdels used, risk estimates varied from the current DHS value, (equivalent to a unit risk of 20 x 10(-5) per ppb), upwards (less risk) at least a factor of 100- old. The different values derived from animal models vary primarily on ths basis of whether or not pharmacokinetic information has been utilized in the assessment. In evaluating the use of pharmacokinetic data Anderson et al. (1980) conclude that: "Based on the present understanding of the mechanism of carcinogenesis, we believe this to be a more rational aplproach to the low-dose extrapolation problem." Gehring et al. (1979) :it a number of extrapolation models to the metabolized dose of VCM, and showed that risk estimates derived without consideration of low-dose metabolite formation potentially overestimate risk by at least an order of magnitude. For example, the one-hit model applied to metabolized dose predicts a risk of 189 per million at 1 ppm for an occupational exposure (Gehring, 1979). By comparison, use of nominal dose (air concentration), predicts upper bounci "risks" of 37,000 per million using the unit risk of 20 x 10(-5) per ppb. Oth ;r viable dose response models predict much lower risk. Not withstanding tl e fact that the health criteria represent one aspect of many inputs consid|ered in the standard setting process, we submit it is essential to base any proposed regulation on the most complete information possible. For this rejason we believe that risk assessments for vinyl chloride should include PK d ta, or preferably, the use of actual human data. Risk assessments derived from epidemiology data In the early 1970's, v nyl chloride was reported to cause a rare form of cancer, angiosarcoma of tl liver, among workers who had been exposed at extremely high le rels for many years in polyvinyl chloride (PVC) polymerization plan s. Since this discovery, there have been approximately 50 angiosarcoma of the liver deaths reported throughout the United States and Canada which have been associated with previous vinyl chloride exposure. Eighty percent of these deaths occurred in four PVC plants where exposures to vinyl c iloride were known to have been over 500 ppm in the 1950's and 1960's. Today, there are strict emission limitations under the NESHAP regulation and the OSHA regulated 8-hour time weighted average for vinyl chloride is ppm. It is particularly noteworthy that there has never been a reported death from angiosarcoma of the liver among Louisiana chemical workers w io have worked with vinyl chloride. Vinyl chloride has i.ot been shown to cause cancer at any other anatomical site in humans. Epiiiemiologic studies conducted in the 1970's suggested that there may be an association with brain and lung cancer, however, recent updates of these stcdies have reported either no association, or associations only at a much lowet statistical level of significance. SPI-00925 -3 - A world-recognized expert in epidemiology. Sir Richard Doll, recently reviewed the existin l vinyl chloride literature as it pertains to cancer in humans. He concl ided that vinyl chloride is a known occupational carcinogen (only for angiosarcoma of the liver) which is due to high occupational exposuie levels which have not existed since this association was reported in the arly 1970's. According to Doll, the risk for cancer in communities surro unding vinyl chloride production plants from environmental emissions in today's tightly controlled and well-regulated environment "must b negligible." (Doll, 1988) Generally, risk asses; ments utilize animal data as the basis for quantification of risk. Human epidemiology data often do not have sufficiently precise exposure estimates or sufficiently well-defined populations to be of quantitative value, Human results are clearly preferred, when available, however, and should be included in any risk assessment review. In the case of VCM there are at least three assessments of sufficient precision which utilize the human di.tabase to estimate risk. In one analysis (Barr, 1982), negative epidemiological studies of people living near VCM production facilities have been used to estimate human potency. Barr estimates that 100 e lifetime dose corresponding to a human risk of 10(-6). Purchase et al. (1987) note that Barr's estimate is similar to the highest estimates of 10(-6) dose levels derived from animal data and are orders of magnitude higher thin the conservative dose estimates which do not take into account low dos i PK. This result is consistent with other observations that humans may be ess sensitive than animals to the carcinogenic effects of VCM. Gehring et al. (1979) compared the results of an epidemiological study of approximately 10,000 occupationally exposed workers to the values predicted by four different mithematical models derived from animal data. They conclude that the observed human results are inconsistent with the two linear non-threshold models used, and are consistent with both the probit model and a linear tl reshold model. The latter two models predict 10*6 risk levels at occupational exposure levels in excess of 1 ppm. These analyses by r o means prove the validity of the two models and undoubtedly numer<b us other models would fit and give quite different results for predicting; the ambient level corresponding to a 10'6 risk level, However, these analysees do show that human epidemiology data can be used to derive risk estimate:s for VCM exposures and that the models indicate that the linear non-thresf old models are conservative by a substantial margin, This is to be expect< d in light of the well known conservativeness of the models. U.S. EPA, ior instance, when presenting risks estimates describes them as upper bound^ and notes that: "the true value of the risk is unknown and may be as low as zero" (Federal Register, 1986). In an analysis of al ernative modeling assumptions for animal to human extrapolation, Elizabeth Anderson, (1984) as head of the U.S. EPA Cancer SPI-00926 1 -4- Assessment Group f:>und that alternative plausible modeling assumptions would lead to risk e:ctimates that were 15-fold to 10,000-fold lower than the standard LMS procec ure. Thus it is essential to use the available human data to place some perspe<:five on the results predicted solely from animal data. In an independent 'eview of VCM, the National Health Council of the Netherlands (1987) derived ambient exposure levels corresponding to risk levels of 10(-6) in hi. mans. Their estimates were derived from both animal data and from epidemiological human data. While noting that the estimates did not differ greatly, they expressed a preference for the human data and reported a value of 1 pg/cubic meter as corresponding to a risk of 10(-6). This value is approximate y 80 times higher than the exposure level derived using the DHS unit risk of 20 x 10(-5) per ppb The over prediction af the models can be further demonstrated for VCM by comparing predictit}ns of risk utilizing the DHS unit risk with human exposure scenarios To make this comparison. Table 1 shows the "risk" predicted from the DHS model for a number of occupational exposure situations. The relevance of the specific exposure scenarios are also discussed below. The specific expos ire scenarios used in Table 1 were based upon a retrospective study Barnes, 1976), in which past typical VCM exposures in PVC plants were estjmated as: 1000 ppm in 1945-1955, 400-500 ppm in 19551960, 300-400 ppm ir 1960-1970, 150 ppm in mid-1973 and considerably lower afterwards. Consid aring the latency of carcinogenesis in general, and for VCM in particular, tumor incidence rates noted in the 1980's reflect exposures from the 1960's. It can be seen froml Table 1 that incidence rates predicted from the linear animal model are completely incompatible with that observed in actual human studies. For example, in the study examined by Gehring (1970) there were only 5 observed cases in 9677 workers. This is approximately three orders of magnitude less than that which would be predicted by the DHS model. Thus, there are a number of assessments based upon human epidemiological data which would indicate that linear models utilizing animal data overpredict risk by at least one to two orders of magnitude. In the interests of assuring that any p imposed regulation is supported by as comprehensive a review of the availasle health data as possible, we submit these assessments should be incorpor ited into any risk assessments which will be used for regulatory control, This is particularly important in view of the fact that they are based upon huir an data rather than on laboratory animal resuits. It can be seen frc m the above analysis that standard risk assessment methodology and tjhe use of reported literature results lead to orders of magnitude over-esti mates of the predicted risk from emissions of VCM from SPI-00927 -5- existing facilities. We recommend that these inconsistencies in the risk estimates be resolved if they are to be used as the basis for any proposed regulation. TABLE 1. "RISK" PREDICTED FROM LMS MODEL (using unit risk of 20 x 10'5 per ppb) Occupational Exposure Scenario Upper Bound on "Risk" (Cases Per 10.000) 400 ppm 30 years 9999 400 ppm 20 years 9995 300 ppm 30 years 9998 300 ppm 20 years 9964 200 ppm 30 years 9960 200 ppm 20 years 9770 100 ppm 30 years 9400 100 ppm 10 years 6090 100 ppm 5 years 3750 SPI-00928 -6- REFERENCES 1. California Air Resouices Board (CARB), Draft Technical Support Document, Proposed Identification of Vinyl Chloride as a Toxic Air Contaminant. May, 1990. 2. Watanabe, P.G., McG wan, G.R., and Gehring, P.J. Fate of [^C] Vinyl Chloride After Single Oral Administration in Rats. Toxicology and Applied Pharmacology 36, 339-352 (1976). 3. Gehring, P.J., Watanale, P.G. and Park, CN. Resolution of Dose-Response Toxicity Data for Chemicals Requir ng Metabolic Activation: Example - Vinyl Chloride. Toxicology and Applied Pharmacology 44, 581-591 (1978). 4. Crump, K.S. Quantita ive Assessment of Human Risk From Exposure to Carcinogens with Special Reference to Vinyl Chloride. Contract for Occupational Health and Safety Division, Ontario Mini stry of Labour (1982). 5. EPA. Incorporation of Biological Information in Cancer Risk Assessment: Example Vinyl Chloride. Office of En rironmental Health and Assessment, US. Environmental Protection Agency. EPA/600/d-B'/188 (1987). 6. Gehring, P.J., Watanafc e, P.G., and Park, C.N. Risk of Angiosarcoma in Workers Exposed to Vinyl Chloride s Predicted from Studies in Rats Toxicology and Applied Pharmacology. Vol. 49, No. 1 (June 15, 1979). 7. Anderson, M.W., Hoel D.G., and Kaplan, N.L. A General Scheme for the Incorporation of Pharmacokinetics in L w-Dose Risk Estimation for Chemical Carcinogenesis: ExampleVinyl Chloride. Toxic ilogy and Applied Pharmacology 55, 154-161 (1980). 8. Federal Register, Volur ie 51, Number 185, Wednesday, September 24,1986. 9. Purchase, I.F.H., Stafford, ]., and Paddle, G.M. Vinyl Chloride: An Assessment of the Risk of Occupational Exposure. Pd. Chem. Toxic. Vol. 25, No. 2, pp. 187-202, 1987. 10. Barr, J.T. Risk Assessment for Vinyl Chloride in Perspective. Presented at the 75th Annual Meeting of the Air Pollution Control Association, New Orleans, USA, (June 1982). 11. National Health Council of The Netherlands. A Scientific Basis for the Risk Assessment of Vinyl Chloride. Re^vlatory Toxicology and Pharmacology 7, 120-127 (1987). 12. Anderson, E.L., Ph.D Risk Analysis in Environmental Health with Emphasis on Carcinogenesis". Harv ird School of Public Health, September 18-20, 1984. 13. Doll, R. Effects of Exposure to Vinyl Chloride: An Assessment of the Evidence, Scand J Work Environment Hea th 14 (1988) 61-78. 14. Maltoni, C. and G. Left mine. Annals of N.Y. Academy of Sciences. 246: 195-218 (1979). 15. Bames, A.W. Vinyl Chbride and the Production of PVC. Proc. R. Soc. Med. 69: 277 (1976). SPI-00929