Interim report of the HELCOM CORESET project

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150 Strand, J, Dahllöf, I. (2005). Biologisk effektmonitering i fi sk. NOVANA teknisk anvisning for marin overvågning, kapitel 6.3. Danmarks Miljøundersøgelser. (In Danish). Strand, J. (2005a). Biologisk effektmonitering i havsnegle og fi sk. Marine workshopper 2004. Research Note from NERI No. 210, 34p. (In Danish) Strand, J. (2005b). Bioligiske effekter i ålekvabbe og muslinger. Marine områder 2004. Status og trends i NOVANA overvågning. Faglig rapport fra DMU. www.dmu.dk. (In Danish). Strand, J. Andersen, L. Dahllöf, I. Korsgaard, B. (2004). Impaired larval development in broods of eelpout (Zoarces viviparus) in Danish coastal waters. Fish Physiology and Biochemistry 30: 37–46 Vetemaa, M. (1999). Reproduction biology of the viviparous blenny (Zoarces vivparus L.). Rep. Nat. Board Fish. Swed. 2: 81-96, Fiskeriverket, Göteborg, Sweden. Vetemaa, M. Förlin, L. Sandström, O. (1997). Chemical effl uent impacts on reproduction and biochemistry in a North Sea population of viviparous blenny (Zoarces viviparus). J. Aquat. Ecosys. Stress Rec. 6: 33-41. Ådjers, K. Appelberg, M. Eschbaum, R. Lappalainen, A. Lozys, L. (2001). Coastal fi sh monitoring in Baltic reference areas 2000. Kala- ja riistaraportteja 229: 1-14, Helsinki, Finland. Agenda item 3 at the HELCOM MONAS meeting 22 – 24 March 2004 in Tallinn, Estonia. Table 3.25. Summary table for reproductive success in eelpout. Evaluation Criteria Rating Description Recommended indicator species - Eelpout (Zoarces viviparus) Recommended matrix - Pregnant females Recommended sample size per station - 40 - 50 fi sh Monitoring guideline (SOP) in place Yes Swedish and Danish monitoring guidelines, ICES guideline in prep. ACs in place, i.e. background response (BaR) Yes BaR 3 countries Available data, spatial coverage in the Baltic Sea - number of countries and stations (20 stations) Available data, length of time series (10 years) Costs of analyses per station, all required individuals (1500EUR) Yes Sweden, Denmark and Germany Medium S: 6-10 stations, DK: 10-15 st. D: 3 st. Good S: 1994-2010, DK: 2002-2010, D: 2003-2009 High ~2000 EUR per station
3.13 B. Reproductive disorders in fi sh and amphipods: Reproductive success in amphipods Authors: Brita Sundelin, Doris Schiedek and Kari Lehtonen ICES SGEH Biological Effects methods Background Documents for the Baltic Sea region (ICES/OSPAR document from the ICES SGIMC Report 2010, complemented and modifi ed by SGEH 2011 with information relevant for application in the Baltic Sea region) Description of the indicator Crustacean amphipods are regularly used in bioassays and laboratory exposure experiments for effects of contaminants. They carry their brood in an egg chamber until hatching and by analyzing the reproduction success we can score the effects of contaminant load in sediment and water. Twenty years of ecotoxicological studies in soft-bottom microcosms and studies of fi eld populations collected in contaminated industrial areas have demonstrated toxicant-sensitive variables on the embryonic development of the Baltic amphipod species Monoporeia affi nis and Pontoporeia femorata (Sundelin 1983, 1984, 1988, 1989, 1998, Eriksson et al. 1996, Eriksson et al. 2005) and other amphipod species (Ford et al. 2003a, Sundelin et al. 2008, Bach et al. 2010). When exposed to heavy metals, chlorinated organic compounds, pulp mill effl uents or contaminated sediments in bioassays as well as in fi eld studies, the frequency of malformed embryos has been demonstrated to be signifi cantly higher when compared to control microcosms and reference areas (Elmgren et al. 1983, Sundelin 1983, 1984, 1988, 1989, 1991, Eriksson et al. 1996, Sundelin & Eriksson 1998, Eriksson et al. 2005) suggesting the variable to be a general bioindicator of contaminant effects. Organic contaminants are often associated to lipids. During oogenesis large quantities of lipids are deposited into the developing oocytes (Herring 1974, Harrison 1990, Harrison 1997, Wouters et al. 2001, Rosa & Nunes 2003). These lipids, which consist mostly of monounsaturated fatty acids, are utilized and consumed during embryo development (Morais et al. 2002, Rosa et al. 2003, 2005), potentially leading to toxic effects of lipophilic contaminants increasing during embryogenesis. These effects also arise in low concentrations that do not demonstrably affect the sexual maturation, fertilization rate, fecundity (eggs/female) and rate of embryo development (time to hatching), indicating embryogenesis to be even more sensitive than other variables of the reproduction cycle. All amphipod species show a similar direct embryo development despite differences in sexual behaviour before mating and in duration of embryogenesis that differs, mainly due to ambient temperature (Bregazzi 1973, Lalitha et al. 1991, McCahon & Pascoe 1988). Therefore, this similar development allows for a consistent method of staging embryogenesis amongst all amphipod species and any resultant aberrations, which makes them particularly good for biomonitoring reproduction effects in situ. Other embryo aberrations respond to oxygen defi ciency, scarcity of food quality and quantity and temperature stress (Eriksson et al. 2001, 2004, Sundelin et al. 2008). Multiple stressors act in concert in the environment and by analysing different types of aberrant embryo development we can discriminate between some of them. The method gives information about health status of the amphipod populations since diseases, parasite infection, sexual maturation in terms of oogenesis in females and sexual development in males and fecundity are scored. Confounding factors Malformed embryos seem to be comparatively insensitive to other environmental stressors but contaminant exposure. However a seven year fi eld study showed a correlation between organic content in the sediment and malformation rate (Eriksson et al. 2004). This could likely depend on higher concentrations 151
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Baltic Sea Environment Proceedings
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2 Helsinki Commission Katajanokanla
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4 4.16. Cumulative impact on benthi
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6 descriptions of the indicators. T
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8 The CORESET expert group on biodi
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10 fi sh stocks and change in diet,
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12 Figure 2.3. The prevalence of pr
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14 Seasonal changes in blubber thic
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16 Blubber thickness suggestions Bl
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18 Weaknesses/gaps Monitoring of th
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20 2.3. Population growth rate of m
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22 Annual adult survival 1 0,95 0,9
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24 Existing monitoring data Informa
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26 References Bäcklin, B. M. 2011.
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28 Reproduction in the Baltic eagle
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30 Breeding success The proportion
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32 of the real number of nestlings
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34 Gaps and weaknesses Minimum dete
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36 2.5. Abundance of wintering popu
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38 Table 2.10. Pressures affecting
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40 Refrences Skov et al. (2000) Bir
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42 termined by application of the 7
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44 Approach for defi ning GES All s
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46 Sampling It is suggested to incl
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48 2.7. Fish population abundance 2
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50 Coastal Fish - Community Abundan
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52 When a reference data set cannot
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54 well, but were not included in t
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56 Weighting For Nordic Costal mult
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58 12. Current monitoring Monitored
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60 Błeńska M., Osowiecki A., Kra
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62 10. Spatial considerations Fucus
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64 2.15. Trend in the arrival of ne
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66 jectives is to reach “No intro
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68 Sweden Figure 2.23 shows the rat
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70 Strengths and weaknesses of data
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72 need to be revisited in light of
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74 Considering the data set availab
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76 In Denmark, the highest contamin
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78 Status of a compound on internat
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80 A temporal analysis (EU-RAR 2006
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82 Pathways of PFOS to the Baltic e
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84 In regions less affected by anth
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86 3.4. Polychlorinated biphenyls a
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88 actions related to the environme
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90 The CORESET expert group decided
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92 pheric deposition pattern (lowes
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94 3.5. Polyaromatic hydrocarbons (
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96 GES boundaries and matrix Existi
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98 Quality Assurance of PAH metabol
Page 102 and 103: 100 Ariese F, Burgers I, Oudhoff K,
Page 104 and 105: 102 GES boundaries and matrices Exi
Page 106 and 107: 104 3.7. Cesium-137 Authors: Jürge
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Page 114 and 115: 112 Conceptual model of the sources
Page 116 and 117: 114 3.8 Tributyltin (TBT) and the i
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Page 120 and 121: 118 Monitoring the compound Status
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Page 124 and 125: 122 3. Frogs have been shown to app
Page 126 and 127: 124 not fi sh (Köhler et al. 2002;
Page 128 and 129: 126 The use of different fi sh spec
Page 130 and 131: 128 Kirchin, M.A. Moore, M.N. Dean,
Page 132 and 133: 130 3.11. Fish Disease Index: Exter
Page 134 and 135: 132 Confounding factors The multifa
Page 136 and 137: 134 analyses ICES data from various
Page 138 and 139: 136 An EAC is the threshold beyond
Page 140 and 141: 138 3.12. Micronucleus test Authors
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Page 144 and 145: 142 ing national data sets. Note: t
Page 146 and 147: 144 Baršienė J. Rybakovas A. 2006
Page 148 and 149: 146 3.13 A. Reproductive disorders
Page 150 and 151: 148 dead larvae can be induced by s
Page 154 and 155: 152 of contaminants in sediments wi
Page 156 and 157: 154 Eriksson Wiklund, A-K., and Sun
Page 158 and 159: 156 4. Candidate indicators for bio
Page 160 and 161: 158 Zooplankton-phytoplankton bioma
Page 162 and 163: 160 4.2. By-catch of marine mammals
Page 164 and 165: 162 4.3. Impacts of anthropogenic u
Page 166 and 167: 164 4.4. Fatty-acid composition of
Page 168 and 169: 166 7. Use of the indicator in prev
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Page 172 and 173: 170 4.10. Large fi sh individuals f
Page 174 and 175: 172 11. Temporal considerations Sam
Page 180 and 181: 178 A proposal for an approach to a
Page 182 and 183: 180 Technical data Metadata This is
Page 184 and 185: 182 F igure 4.1. Map showing the cu
Page 186 and 187: 184 4.17. Biomass of copepods 1. Wo
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Page 192 and 193: 190 Notes for the GES boundary The
Page 194 and 195: 192 Step 3: Prepare a list of speci
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200 4.27. EROD/CYP1A induction The
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202 5.1. Summary of all supplementa
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204 Table 5.1. (continues) Suppleme
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206 5.5. Biopollution level index 1
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208 NIS for aquaculture purposes. O
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210 Balanus improvisus Baltic Katte
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212 Figure 5.3. The scheme for asse
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214 5.6. Organochlorine compounds G
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216 EU Directive 2008/105/ EC Daugh
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218 Table 5.4. Monitoring of HCB, H
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