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Issues in Risk Assessment (1993)
Commission on Life Sciences (CLS)

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. "OPTION 3." Issues in Risk Assessment. Washington, DC: The National Academies Press, 1993.

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Issues in Risk Assessment

If the numbers of animals in a test were not substantially increased, agents that were formerly found to be carcinogenic only at the MTD would not be identified as positive in this procedure. Thus, this procedure would focus attention on agents that had high carcinogenic potency relative to their subacute toxicity (Region C carcinogens in Figure 1).

An advantage of this procedure is a flexibility that reflects differences between potentially hazardous substances themselves or the expected exposures of humans to them. Most such chemicals will never be tested in chronic animal bioassays; current evidence suggests that, if they were, about half would be identified as carcinogens and almost all, by definition, would be in Region B. It would clearly pose a dilemma for regulators to be faced with decisions on a multitude of chemicals that would be identified as carcinogens under today's regulatory standards. However, substances with low toxicity but high carcinogenic potency (Region C carcinogens) might well present an unusually high cancer risk to human populations but not produce toxicity in the bioassay that serves to warn people of a hazard; that is apparently what happened with vinyl chloride workers (Fox and Collier, 1977; IARC, 1979).

A disadvantage of this option is that it would decrease the sensitivity of the assay, thus reducing its usefulness as a means of hazard identification. This disadvantage can be compensated for by increasing the numbers of animals in test groups; however, the expense of increasing the number of animals to a point necessary to retain the same power would probably be prohibitive. Furthermore, the choice of a lower dose, such as MTD/3, as the highest dose is arbitrary. Although implementation of this option would identify primarily Region C carcinogens, there is little evidence that Region C carcinogens contribute a predominant portion of chemically induced cancer risk to human populations. Future uses of a chemical cannot always be anticipated. If the HDT were based on current uses, a future use that entailed high human exposures could necessitate a new bioassay.

OPTION 3

Base the HDT on preliminary studies that determined the dose dependence of physiologic effects induced by the chemical and the dose dependence of its metabolism.

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55
Front Matter (R1-R18)
Executive Summary (1-2)
USE OF THE MAXIMUM TOLERATED DOSE IN ANIMAL BIOASSAYS FOR CARCINOGENICITY (3-8)
THE TWO-STAGE MODEL OF CARCINOGENESIS (9-9)
A PARADIGM FOR ECOLOGIC RISK ASSESSMENT (10-12)
Issues In Risk Assessment Use Of Maximum Tolerated Dose in Animal Bioassays for Carcinogenicity (13-14)
BACKGROUND (15-17)
SCOPE OF REPORT (18-20)
DEFINITIONS AND BACKGROUND (21-23)
CORRELATIONS (24-32)
RELATIONSHIP BETWEEN TOXICITY AND CARCINOGENICITY OBSERVED AT MTD (33-42)
QUALITATIVE INFORMATION (43-48)
QUANTITATIVE INFORMATION (49-52)
OPTION 1 (53-53)
OPTION 2 (54-54)
OPTION 3 (55-56)
Option 4A (57-58)
Option 4B (59-60)
5 Conclusions and Recommendations (61-66)
REFERENCES (67-78)
BACKGROUND (79-79)
DEFINING AND DETERMINING THE MTD (80-90)
Appendix B Organizing Subcommittee (91-92)
Appendix C Federal Liaison Group (93-94)
Appendix D Workshop Program (95-96)
Appendix E Workshop Attendees (97-110)
1. INTRODUCTION (111-112)
2.1 Measures of Carcinogenic Potency (113-115)
2.2 Carcinogenic Potency Database (CPDB) (116-116)
2.3 Variation in Carcinogen Potency (117-118)
2.4 Classification of Carcinogens (119-120)
3.1 Empirical Correlations (121-124)
3.2 Range of Possible TD50 Values (125-125)
3.3 Analytical Correlations (126-127)
3.4 Model Dependency (128-129)
3.5 Genotoxic vs. Nongenotoxic Carcinogens (130-130)
4.1 Predictions Based on the MDT (131-131)
4.2 Predictions Based on Mutagenicity and Acute Toxicity (132-134)
5.1 Correlation Between Upper Bounds On the Low Dose Slope and MTD (135-135)
5.2 Correlation Between q1* and the TD50 (136-138)
5.3. Preliminary Estimate of Risk (139-139)
6. INTERSPECIES EXTRAPOLATION (140-140)
6.1 Extrapolation from Rats to Mice (141-143)
6.2 Extrapolation from Rodents to Humans (144-145)
7. CONCLUSIONS (146-148)
8. ACKNOWLEDGEMENTS (149-149)
9. REFERENCES (150-159)
ANNEX A: MAXIMUM LIKELIHOOD METHODS FOR FITTING THE WEIBULL MODEL (160-161)
ANNEX B. SHRINKAGE ESTIMATORS OF THE DISTRIBUTION OF CARCINOGENIC POTENCY (162-163)
ANNEX C: ADJUSTMENT OF POTENCY VALUES FOR LESS THAN LIFETIME EXPOSURE (164-165)
ANNEX D: CORRELATION BETWEEN TD50 AND MTD (166-168)
ANNEX E: CORRELATION BETWEEN TD50S FOR RATS AND MICE (169-172)
Appendix G Informal Search for ''Supercarcinogens" (173-174)
CRITERIA AND CANDIDATE CHEMICALS (175-176)
DATA (177-180)
RESULTS (181-181)
DISCUSSION (182-184)
Issues in Risk Assessment The Two-Stage Model Of Carcinogenesis (185-186)
INTRODUCTION (187-187)
BIOLOGIC CONSIDERATIONS (188-189)
THE TWO-STAGE MODEL (190-195)
APPLICATIONS OF THE TWO-STAGE MODEL TO ANIMAL DATA (196-211)
Data Needs (212-212)
Criteria for Adoption (213-213)
Prospects (214-214)
CONCLUSIONS AND RECOMMENDATIONS (215-216)
REFERENCES (217-222)
BIOLOGICAL FACTORS IN TWO-STAGE MODELS (223-225)
TWO-STAGE MODEL OF CLONAL EXPANSION (226-227)
APPLICATION OF THE TWO-STAGE MODEL TO ANIMAL DATA (228-232)
Appendix B Workshop Program (233-234)
Appendix C Workshop Federal Liaison Group (235-236)
TOPIC GROUP MEMBERS (237-238)
Appendix E Workshop Organizing Task Group (239-240)
Isuees In Risk Assessment A Paradigm for Ecological Risk Assessment (241-242)
1 Introduction (243-246)
2 Scope of Ecological Risk Assessment (247-248)
COMPONENTS OF THE 1983 FRAMEWORK (249-250)
CONSISTENCY OF CASE STUDIES WITH THE 1983 FRAMEWORK (251-253)
INTEGRATION OF ECOLOGICAL RISK INTO THE 1983 FRAMEWORK (254-254)
DEFINITION OF FRAMEWORK COMPONENTS FOR ECOLOGICAL RISK ASSESSMENT (255-258)
EXTRAPOLATION ACROSS SCALES (259-260)
QUANTIFICATION OF UNCERTAINTY (261-261)
VALIDATION OF PREDICTIVE TOOLS (262-262)
VALUATION (263-264)
5 Conclusions (265-266)
6 Recommendations (267-268)
REFERENCES (269-272)
Appendix A Workshop Participants (273-278)
Appendix B Workshop Organizing Subcommittee and Federal Liaison Group (279-280)
Appendix C Workshop Introduction (281-282)
TERRY F. YOSIE BUILDING ECOLOGICAL RISK ASSESSMENT AS A POLICY TOOL (283-285)
D. WARNER NORTH: RELATIONSHIP OF WORKSHOP TO NRC'S 1983 RED BOOK REPORT (286-288)
MICHAEL SLIMAK: U.S. ENVIRONMENTAL PROTECTION AGENCY ACTIVITIES IN ECOLOGICAL RISK ASSESSMENT (289-292)
CASE STUDY 1: TRIBUTYLTIN RISK MANAGEMENT IN THE UNITED STATES (293-293)
Discussion (294-294)
CASE STUDY 2: ECOLOGICAL RISK ASSESSMENT FOR TERRESTRIAL WILDLIFE EXPOSED TO AGRICULTURAL CHEMICALS (295-296)
CASE STUDY 3A: MODELS OF TOXIC CHEMICALS IN THE GREAT LAKES: STRUCTURE, APPLICATIONS, AND UNCERTAINTY ANALYSIS (297-298)
CASE STUDY 3B: ECOLOGICAL RISK ASSESSMENT OF TCDD AND TCDF (299-299)
Discussion (300-300)
CASE STUDY 4: RISK ASSESSMENT METHODS IN ANIMAL POPULATIONS: THE NORTHERN SPOTTED OWL AS AN EXAMPLE (301-301)
Discussion (302-302)
CASE STUDY 5: ECOLOGICAL BENEFITS AND RISKS ASSOCIATED WITH THE INTRODUCTION OF EXOTIC SPECIES FOR BIOLOGICAL CONTROL OF A... (303-303)
Discussion (304-304)
CASE STUDY 1: UNCERTAINTY AND RISK IN AN EXPLOITED ECOSYSTEM: A CASE STUDY OF GEORGES BANK (305-306)
Discussion (307-308)
Generic Issues (309-309)
Analysis of Case Studies (310-310)
DOSE-RESPONSE ASSESSMENT (311-311)
Selection of End Points (312-312)
Consideration of Nonlinearities And Discontinuities (313-313)
Understanding the Stressor (314-314)
Additions to the 1983 Paradigm Needed for Ecological Risk Assessment (315-315)
Modeling Needs for Stress-Response Relationships (316-316)
Methods of Measuring Stressors for Ecological Exposure Assessment (317-317)
Definition of Risk Characterization (318-318)
Components of Risk Characterization (319-319)
Organization and Presentation (320-320)
Differences from and Similarities To the 1983 Report (321-321)
Application to the Case Studies (322-323)
Agricultural Chemicals (324-324)
Northern Spotted Owl (325-325)
General Discussion: Models and Risk Assessment (326-326)
Uncertainties Identified In the Case Studies (327-327)
Implications of Uncertainty for Ecological Risk Assessment (328-328)
VALUATION (329-330)
Risk Assessment Has Many Uses (331-332)
Different Risk Assessment Methods Are Suited to Different Risk Assessment Needs (333-333)
Risk Assessors and Risk Managers Need to Communicate (334-334)
Credibility is Crucial (335-336)
Appendix G Contemplations on Ecological Risk Assessment (337-342)
Appendix H Workshop Summary (343-346)
Appendix I References for Appendixes (347-350)
Appendix J Workshop Program (351-356)

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OCR for page 55
Issues in Risk Assessment If the numbers of animals in a test were not substantially increased, agents that were formerly found to be carcinogenic only at the MTD would not be identified as positive in this procedure. Thus, this procedure would focus attention on agents that had high carcinogenic potency relative to their subacute toxicity (Region C carcinogens in Figure 1). An advantage of this procedure is a flexibility that reflects differences between potentially hazardous substances themselves or the expected exposures of humans to them. Most such chemicals will never be tested in chronic animal bioassays; current evidence suggests that, if they were, about half would be identified as carcinogens and almost all, by definition, would be in Region B. It would clearly pose a dilemma for regulators to be faced with decisions on a multitude of chemicals that would be identified as carcinogens under today's regulatory standards. However, substances with low toxicity but high carcinogenic potency (Region C carcinogens) might well present an unusually high cancer risk to human populations but not produce toxicity in the bioassay that serves to warn people of a hazard; that is apparently what happened with vinyl chloride workers (Fox and Collier, 1977; IARC, 1979). A disadvantage of this option is that it would decrease the sensitivity of the assay, thus reducing its usefulness as a means of hazard identification. This disadvantage can be compensated for by increasing the numbers of animals in test groups; however, the expense of increasing the number of animals to a point necessary to retain the same power would probably be prohibitive. Furthermore, the choice of a lower dose, such as MTD/3, as the highest dose is arbitrary. Although implementation of this option would identify primarily Region C carcinogens, there is little evidence that Region C carcinogens contribute a predominant portion of chemically induced cancer risk to human populations. Future uses of a chemical cannot always be anticipated. If the HDT were based on current uses, a future use that entailed high human exposures could necessitate a new bioassay. OPTION 3 Base the HDT on preliminary studies that determined the dose dependence of physiologic effects induced by the chemical and the dose dependence of its metabolism.

OCR for page 56
Issues in Risk Assessment In this option, a comprehensive series of tests would be conducted before the bioassay were initiated. The tests would be designed to provide information about mechanisms of toxicity, as well as the dose-response curve for such toxicity. Microscopic examination of tissues would continue to be a part of studies, as would clinical chemistry (e.g., serum enzyme measurements and urinalysis.) However, the studies would be expanded to include measurement of physiologic and biochemical effects (e.g., alterations in hormone status) and quantitative measurements of cell proliferation. In addition, extensive pharmacokinetic studies (quantitative measurements of uptake, distribution, metabolism, and elimination) would be carried out. An expert panel would be convened to evaluate preliminary data before doses for the bioassay were selected. The panel would select the HDT and lower doses on the basis of evaluation of the preliminary studies. The objective would be to design a study that could be expected to yield results that would be useful for human risk assessment and not simply to administer as much chemical as possible without causing early mortality from causes other than cancer. This approach constitutes a change in emphasis of the bioassay. Studies that use the MTD as currently defined are designed to maximize the sensitivity of the bioassay (i.e., to prevent false-negative results). The objective of the new approach would be to increase the selectivity of the bioassay (i.e., to decrease the number of false-positive results). In some cases, adoption of this option would not change the selection of the MTD as the HDT. For example, if human populations were reasonably expected to encounter high concentrations of the test substance, the MTD would continue to be used. In many cases, however, the HDT would be lower than the MTD as currently defined, and the spacing of doses could be much wider than commonly adopted by programs such as the National Toxicology Program (NTP). An advantage of this modification is that the mechanisms underlying any observed carcinogenic response would be more likely to be qualitatively and quantitatively similar to those operating at lower doses than mechanisms underlying responses observed at the MTD. A disadvantage of this modification might be that doses that caused a physiologic change in one organ might not cause physiologic changes in other organs. Without knowledge of the target sites for carcinogenicity, it would be unclear whether a physiologic change that is being avoided