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

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. "Option 4A." Issues in Risk Assessment. Washington, DC: The National Academies Press, 1993.

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Issues in Risk Assessment

by testing at lower doses has any relevance to those other target sites. For example, if an HDT were selected to be below a dose that caused a physiologic change in the liver but not the lung, one could miss a carcinogenic effect on the lung at a dose that does not alter lung physiology.

OPTION 4

Use MTD testing as part of an overall testing strategy.

The animal bioassay that uses the MTD is one part of a complete program for identifying human carcinogens. It generally is conducted after some indication that a substance merits examination—e.g., information that a chemical has a structural similarity to a known carcinogen, results of a test for mutagenicity, or a suggestion that there will be extensive human exposure to the substance. It is then used as a screening technique to separate carcinogens from noncarcinogens it can be followed by tests to determine mode of action, pharmacokinetics, and applicability of results to the human experience. The workshop participants and the committee discussed two-ways to use the MTD test in a complete program. They are described below.

Option 4A

Use a two-track system that comprises full testing and limited testing.

In this option, chemicals would be placed into two-tracks for testing. A small number of selected chemicals would be subjected to rigorous testing (the full-testing track). All the remaining chemicals would be subjected to less rigorous testing (the limited-testing track). The option is based on three premises:

  • A large amount of additional information might be needed to assist in understanding the importance of positive results at the MTD.

  • It might not be feasible to collect the additional information for all the chemicals whose regulation is appropriate.

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57
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 57
Issues in Risk Assessment by testing at lower doses has any relevance to those other target sites. For example, if an HDT were selected to be below a dose that caused a physiologic change in the liver but not the lung, one could miss a carcinogenic effect on the lung at a dose that does not alter lung physiology. OPTION 4 Use MTD testing as part of an overall testing strategy. The animal bioassay that uses the MTD is one part of a complete program for identifying human carcinogens. It generally is conducted after some indication that a substance merits examination—e.g., information that a chemical has a structural similarity to a known carcinogen, results of a test for mutagenicity, or a suggestion that there will be extensive human exposure to the substance. It is then used as a screening technique to separate carcinogens from noncarcinogens it can be followed by tests to determine mode of action, pharmacokinetics, and applicability of results to the human experience. The workshop participants and the committee discussed two-ways to use the MTD test in a complete program. They are described below. Option 4A Use a two-track system that comprises full testing and limited testing. In this option, chemicals would be placed into two-tracks for testing. A small number of selected chemicals would be subjected to rigorous testing (the full-testing track). All the remaining chemicals would be subjected to less rigorous testing (the limited-testing track). The option is based on three premises: A large amount of additional information might be needed to assist in understanding the importance of positive results at the MTD. It might not be feasible to collect the additional information for all the chemicals whose regulation is appropriate.

OCR for page 58
Issues in Risk Assessment Without accompanying information on mechanisms or results at low doses, animal bioassay results alone (i.e., without parallel data on mechanisms and dose-response relationships) do not add greatly to our ability to make regulatory decisions because of the uncertainty about the human implications of positive results in animal bioassays. Chemicals could be chosen for full testing on the basis of expected human exposures, importance in commerce, structural similarity to a known carcinogen, or results of mutagenicity tests—i.e., in much the same way that chemicals are currently chosen for testing. The method of Gaylor (1989), basing a preliminary estimate of the carcinogenic potency of a chemical on its MTD, could also be used to select chemicals for full or limited testing. As described earlier, given the relationship between the carcinogenic potency of chemicals and their MTDs, Gaylor pointed out that a preliminary estimate of the dose corresponding to a carcinogenic risk of one in a million human lifetimes could be found by dividing the MTD by 380,000. If human exposures were unlikely to be greater than the quotient, the chemical would not be assigned to full testing on the grounds that, even if it were a carcinogen, human risk would be unlikely to be greater than one in a million per lifetime. (A different divisor could be selected if a level of safety different from one in a million per lifetime were required.) When a class of structurally similar chemicals that are thought likely to have similar mechanisms of action is being considered, it might be a good use of resources to test fully only a small number (perhaps only one) of representative chemicals in the class and to evaluate the others in the class for relative potency on the basis of data from short-term, less-expensive studies. Chemicals chosen for full testing would be tested in a standard bioassay that used the MTD and an array of doses below the MTD. If a chemical were positive, additional testing would be performed as needed to clarify the dose-response relationship and to improve the predictive value of the positive findings for humans. Chemicals chosen for limited testing would be considered for regulation without testing in a long-term cancer bioassay. Regulatory decisions for these chemicals would be based on more limited data, such as estimates of the MTD from short-term studies, mutagenicity information, and other data that can be gathered much more quickly and cheaply than results from a lifetime bioassay.