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APPENDIX VIII homeostatic regulation capacity will be exceeded at a given higher external concentration beyond which the element will accumulate and become toxic. Risk Characterisation The risk characterisation of metals basically follows the principles set out in Section 4 of the main text. However, it should be stated again that is very important that both PEC and PNEC are based on similar levels of availability. In addition, when PEC/PNEC ratios greater than one are found, it is very important to have information on the natural and/or ambient background levels in order to decide upon further actions to be taken to reduce the risks. Since for most metals sufficient monitoring data are obtainable, risk assessment will often be based on measured instead of calculated environmental concentrations, especially for a regional assessment. Usually most monitoring data deal with total concentrations. Especially in case of aqueous systems it often is well possible to convert measured total concentrations to dissolved concentrations. For terrestrial systems this is possible by applying the appropriate Kp values. References Cleven RFMJ, Janus JA, Annema JA and Slooff W (eds.) (1993). Integrated Criteria Document Zinc. RIVM report No. 710401028. Luoma SN (1983). Bioavailability of trace metals to aquatic organisms - a review. The Science of the Total Environment 28, 1-22. Ministry of VROM (1994). Environmental Quality Objectives in the Netherlands, Den Haag, The Netherlands. Ontwerp-uitvoeringsbesluit bij het vlaamse bodemsaneringsdecreet (24-01-1995) houdende achtergrondwaarden en bodemsaneringsnormen (document on background concentrations in Flanders, Belgium). Parametrix Inc. (draft February 1995). Aquatic Ecotoxicity Testing of Sparingly Soluble Metals and Metal Compounds. Prepared for the Mining Association of Canada, Washington. Ure AM, Davidson CM (eds.) (1995). Chemical Speciation in the Environment. Blackie Academic & Professional, Glasgow. Van der Kooij LA, van de Meent D, van Leeuwen CJ, Bruggeman WA (1991). Deriving quality criteria for water and sediment from the results of aquatic toxicity test and product standards: application of the equilibrium partitioning method. Wat. Res. 25, 697-705. Van Tilborg WJM and van Assche F (1995). Integrated Criteria Document Zinc: Industry Addendum. Projectgroep Zink BMRO-VNO, Roozendaal. Van Wensem J, Vegter JJ, van Straalen NM (1994). Soil quality derived from critical body concentrations of metals in soil invertebrates. Appl. Soil Ecol. 1, 185-191. Wood JM (1974). Biological cycles for toxic elements in the environment. Science 188, 1049-1052. 310
Appendix IX Environmental risk assessment for petroleum substances Introduction APPENDIX IX In the present appendix the Hydrocarbon Block Method (HBM) is described, which is under development and may be used for environmental risk assessment of petroleum substances. The method was originally devised by CONCAWE (The Oil Companies' European Organisation for Environmental and Health Protection) and was discussed in a workshop in Ispra in December 1994 (CONCAWE, 1995; EU, 1995). The approach has only recently been devised and hence experience with its application is limited. Although there has been work to validate the general approach, it should be recognised that there are still uncertainties regarding some technical details which should be borne in mind, when considering the outcome of the risk characterisation. Outline of the method There are many petroleum substances (e.g. refinery streams and solvents) which although described by a single EINECS number are hydrocarbon mixtures of varying degrees of complexity. The compositional complexity of many petroleum hydrocarbon substances is compounded by the fact that their composition will vary depending on the source of crude oil and the details of the process used in their production. This compositional complexity poses particular problems when environmental risk assessment is required. Difficulties in carrying out a risk assessment for petroleum substances arise because individual components of them have specific and different physico-chemical and ecotoxicological properties, and potentials to be degraded in the environment. Each will be subjected to different distribution and fate processes on release. This means that on release to the environment, each component will behave independently and reach its own concentration in each environmental compartment. It follows from this, that a PEC for the whole petroleum substance does not exist. It would in theory, be possible to identify each individual component of a petroleum substance and then to determine a PEC for each of them. In practice this approach demands a degree of analytical resolution that is not achievable for most petroleum substances and even where possible, handling such large quantities of data would be impractical. However, since hydrocarbons of similar structure will have similar physico-chemical properties and potentials to be degraded in the environment they will have similar distributions and fates within a given environment. It is therefore possible to group or “block” such hydrocarbons, so that components having similar properties may be considered together (it should be recognised that a “block” may consist of a single component or a large number of components with similar fate and distribution properties). Once the “blocks” for a substance have been established, PEC values can be calculated for each “block” for each environmental compartment. Given that PECs can only be obtained for single components , or groups of similar components, it follows that PNECs must also be estimated for the same individual components or groups of components. Therefore, ecotoxicity data obtained on the whole substance, whether obtained using water accommodated fractions (WAFs) or dispersions, cannot be used to estimate PNECs. PNECs must be based on the toxicity of the individual “blocks”, be they single or multiple component “blocks”. These blocks should show similar modes of action. From the above it is clear that the PEC/PNEC ratio of the whole substance cannot be derived directly, as neither the PEC, nor the PNEC for the whole substance will be available. The PEC/PNEC ratio is therefore derived from the PEC/PNEC ratios of the “blocks” of components, 311
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Institute for Health and Consumer P
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LEGAL NOTICE Neither the European C
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OVERVIEW This Technical Guidance Do
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CONTENTS 1 GENERAL INTRODUCTION ...
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4.2.3.4 Use of biodegradation scree
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1 GENERAL INTRODUCTION 1.1 BACKGROU
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GENERAL INTRODUCTION countries in t
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GENERAL INTRODUCTION PNEC is regard
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2 ENVIRONMENTAL EXPOSURE ASSESSMENT
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ENVIRONMENTAL EXPOSURE ASSESSMENT r
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2.2 MEASURED DATA ENVIRONMENTAL EXP
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ENVIRONMENTAL EXPOSURE ASSESSMENT w
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ENVIRONMENTAL EXPOSURE ASSESSMENT o
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ENVIRONMENTAL EXPOSURE ASSESSMENT T
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ENVIRONMENTAL EXPOSURE ASSESSMENT r
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Production ENVIRONMENTAL EXPOSURE A
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Back to processing Product at end o
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ENVIRONMENTAL EXPOSURE ASSESSMENT s
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Explanation of symbols ENVIRONMENTA
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ENVIRONMENTAL EXPOSURE ASSESSMENT s
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ENVIRONMENTAL EXPOSURE ASSESSMENT U
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ENVIRONMENTAL EXPOSURE ASSESSMENT a
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ENVIRONMENTAL EXPOSURE ASSESSMENT F
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2.3.5.1 Adsorption to aerosol parti
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ENVIRONMENTAL EXPOSURE ASSESSMENT I
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2.3.6.1 Hydrolysis ENVIRONMENTAL EX
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2.3.6.3 Photochemical reactions in
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constant of zero. However, if it ca
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ENVIRONMENTAL EXPOSURE ASSESSMENT A
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ENVIRONMENTAL EXPOSURE ASSESSMENT a
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Primary Settler Aeration Tank 2 5 3
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ENVIRONMENTAL EXPOSURE ASSESSMENT I
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ENVIRONMENTAL EXPOSURE ASSESSMENT d
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ENVIRONMENTAL EXPOSURE ASSESSMENT e
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Table 10 Overview of different expo
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ENVIRONMENTAL EXPOSURE ASSESSMENT -
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2.3.8.3 Calculation of PEClocal for
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ENVIRONMENTAL EXPOSURE ASSESSMENT W
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Guidance for calculating PEClocal i
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Concentration (% of initial) 160 14
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Calculation of PEClocalsoil For soi
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ENVIRONMENTAL EXPOSURE ASSESSMENT
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Output ENVIRONMENTAL EXPOSURE ASSES
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3 EFFECTS ASSESSMENT 3.1 INTRODUCTI
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3.2.1.1 Completeness of data New su
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EFFECTS ASSESSMENT • it is clearl
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EFFECTS ASSESSMENT 3.3 EFFECTS ASSE
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Table 16 Assessment factors to deri
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Input data EFFECTS ASSESSMENT The m
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Estimation of the PNEC The PNEC is
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EFFECTS ASSESSMENT biodegradability
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Table 17 Test systems for derivatio
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EFFECTS ASSESSMENT representative o
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In the partitioning method, it is a
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EFFECTS ASSESSMENT As mentioned in
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3.6.2.1 Calculation of PNEC using t
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3.7 EFFECTS ASSESSMENT FOR THE AIR
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EFFECTS ASSESSMENT procedure availa
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EFFECTS ASSESSMENT bioaccumulation
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EFFECTS ASSESSMENT For some chemica
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EFFECTS ASSESSMENT i.e. without enh
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Conversion factors for laboratory a
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EFFECTS ASSESSMENT • relative sen
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EFFECTS ASSESSMENT Earthworms are a
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MARINE RISK ASSESSMENT environment
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MARINE RISK ASSESSMENT of equal rel
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4.2.3.3 Marine biodegradation simul
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MARINE RISK ASSESSMENT In addition
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Explanation of symbols MARINE RISK
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MARINE RISK ASSESSMENT evaluate the
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MARINE RISK ASSESSMENT marine water
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MARINE RISK ASSESSMENT The addition
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MARINE RISK ASSESSMENT Statistical
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MARINE RISK ASSESSMENT sediment, fo
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Table 27 Assessment factors for der
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Table 28 continued Acute and chroni
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MARINE RISK ASSESSMENT of different
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MARINE RISK ASSESSMENT • a measur
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MARINE RISK ASSESSMENT b. the conce
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MARINE RISK ASSESSMENT mechanisms s
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MARINE RISK ASSESSMENT The use of t
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4.4.4.2 Assessment of measured BCF
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MARINE RISK ASSESSMENT required to
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Table 33 Overview of PEC/PNEC ratio
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RISK CHARACTERISATION If a refineme
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Classified dangerous to the Environ
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RISK CHARACTERISATION eaters. This
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6 TESTING STRATEGIES 6.1 INTRODUCTI
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TESTING STRATEGIES Performance of a
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TESTING STRATEGIES Care must be tak
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Algal testing Algae toxicity test (
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TESTING STRATEGIES • long-term te
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Microbial assays TESTING STRATEGIES
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TESTING STRATEGIES A soil bioassay
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REFERENCES Brandes LJ, den Hollande
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REFERENCES IPCS (2000). Framework f
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REFERENCES OECD (1984f). Activated
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REFERENCES Pack S. (1993). A review
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REFERENCES US EPA (1996). Whole Sed
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APPENDIX I volume imported in the E
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APPENDIX I MC IV “Wide dispersive
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APPENDIX I 210 Stage Main category
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APPENDIX I the number of days over
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APPENDIX I Stage Main category Ia I
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APPENDIX I manufacturing of motor c
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APPENDIX I 1. extension of the tabl
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APPENDIX I 220 A-tables Estimates f
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APPENDIX I PRIVATE USE Not applicab
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APPENDIX I IC = 3: CHEMICAL INDUSTR
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APPENDIX I IC = 5: PERSONAL /DOMEST
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APPENDIX I Table A4.1 continued Com
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APPENDIX I IC = 7: LEATHER PROCESSI
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APPENDIX I IC = 9: MINERAL OIL AND
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APPENDIX I WASTE TREATMENT Table A5
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APPENDIX I For the emission factors
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APPENDIX I INDUSTRIAL USE Table A3.
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APPENDIX I INDUSTRIAL USE Table A3.
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APPENDIX I PRIVATE USE Table A4.5 C
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APPENDIX I PRIVATE USE Table A3.16
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APPENDIX I 246 B-tables Estimates f
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APPENDIX I FORMULATION Table B2.2 f
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APPENDIX I IC = 3: CHEMICAL INDUSTR
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APPENDIX I IC = 5: PERSONAL/DOMESTI
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APPENDIX I IC = 7: LEATHER PROCESSI
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APPENDIX I IC = 9: MINERAL OIL AND
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APPENDIX I IC = 11: POLYMERS INDUST
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