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146 3.13 A. Reproductive disorders in fi sh and amphipods: Reproductive success in eelpout Authors: Jakob Strand, 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 Eelpout (Zoarces viviparus), also called viviparous blenny, is a benthic fi sh species that is widely used in ecotoxicological studies and as a bioindicator of local pollution due to its stationary behaviour in coastal marine environment. Eelpout is a recommended fi sh indicator species for assessing the environmental conditions in the Baltic Sea and eelpout is included in the environmental monitoring programmes of several Baltic States, both in relation to biological effects, contaminants and integrated fi sh monitoring. For instance, Sweden and Germany have routinely measured contaminant concentrations in eelpout for >15 years, and additional samples are archived in environmental specimen banks allowing retrospective studies on chemical burdens. Similar long time series is also available for some other biomarker studies. The eelpout is viviparous, i.e. there is an internal fertilization of the eggs and the female fi sh gives birth to fully developed larvae. The eelpout’s mode of reproduction (vivipari) enables the study of “reproductive success” on an individual level, and larval developmental disorders can be directly associated with e.g. the health status of the female or body burdens of toxic substances during pregnancy. Different types of abnormal larvae development can be distinguished and be characterised into different groups, i.e. early dead embryos, late dead larvae, growth retarded larvae and deformed larvae, which can be divided into different subgroups of severe gross malformations. Reproductive success in eelpout as a biological effects method is regarded as a general, i.e. non-specifi c, integrative indicator for impaired fi sh reproduction, and a signifi cant biological endpoint for assessing potential population-relevant effects. Because the reproductive success in fi sh is a generic “stress” indicator; causal agents may, however, only be identifi ed through a combination of chemical analyses of fi sh tissue and also other biological effects measurements. Several types of hazardous substances such as organochlorines, pesticides, PAH, heavy metals and organometals are known to have the potential to affect embryo and larval development in fi sh, generally (Bodammer 1993). Several of these substances, which may induce developmental, morphological and/or skeletal anomalies, have also been identifi ed as endocrine disrupting substances (Davis 1997). Reproductive success in eelpout is included in the list of parameters for biological effect monitoring for supporting programme in the HELCOM COMBINE manual for marine monitoring in the coastal zone. Part D. Programme for monitoring of contaminants and their effects (HELCOM 2006). The method is also part of OSPAR pre-CEMP and JAMP guideline for general biological effects monitoring (OSPAR 2010). According to the monitoring guideline, the sample size should consist of examinations of 40 – 50 individuals of pregnant females of eelpout per station, which should be sampled in the period between October 15 and December 1.
There is in some countries restrictions on eelpout fi shery that depends on national legislations, e.g. fi shing dispensation for catching pregnant females in the autumn is needed in Denmark. National concerns for impact of fi shery on local populations and ethical guidelines for humane handling and fi sh killing should also be considered. In the Baltic Sea region, reproductive success in eelpout is or has been used for monitoring or pre-monitoring investigations at least by labs from Denmark, Sweden, Germany and Poland and as part of integrated fi sh monitoring, often in combination with contaminant, biomarker studies and/or population studies. Studies in the Baltic Sea has shown that that spatial differences occur with elevated levels of adverse developmental effects of embryo and larvae in eelpout broods have been found in populations living in contaminated areas with effl uents from cities and industry. In comparison, only low levels of such effects generally occur in populations living in areas regarded as reference sites (e.g. Vetemaa et al. 1997, Ådjers et al. 2001, Sjölin et al. 2003, Strand et al. 2004, Kalmarweb 2005, Gercken et al. 2006) as shown in Figure 3.13. Mean frequency (%) of abnormal larvae 15 10 5 0 - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - ----- ----- Reference sites Not reference sites - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - ----- - - - - - - - - - - - ----- Reference sites Not reference sites Reference sites Max.-value 90% percentile ---- Median 10% percentile Min.-value - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - - Not reference sites Late dead larvae Malformed larvae Retarded larvae Figure 3.13. Comparison of data distribution of compiled monitoring data on mean frequencies of late dead, malformed and growth retarded larvae in eelpout broods from reference sites and area not regarded as reference sites. The blue dotted line refers to the 90% percentile of data from the reference sites. The red dotted line refers to signifi cantly elevated levels compared to the 90% percentile of the reference sites. Clear temporal developments with up- or down-going trends for the presence of different types of abnormal larvae development have not been established in monitored baseline areas with longer time series. However, some year-to-year variations can occur. Studies of point sources have shown that acute larval mortality also been observed in eelpout exposed to pulp mill effl uents (Jacobsson et al. 1986). Skewed sex ratios with signifi cant more males in the eelpout broods have also been found nearby pulp mill effl uents indicating effects of endocrine disruption substances (Larsson & Förlin 2002). Confounding factors Other environmental stressors like increased temperature and severe oxygen depletion events may however also affect eelpout reproduction (Veetema 1999, Fagerholm 2002, Strand et al. 2004). There have been some indications that some specifi c types of abnormal larvae development like early dead embryos and late ----- ----- 147
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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 (
Page 98 and 99: 96 GES boundaries and matrix Existi
Page 100 and 101: 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
Page 108 and 109: 106 Figure 3.5. Average surface lev
Page 110 and 111: 108 Temporal trends in concentratio
Page 112 and 113: 110 Other important sources are glo
Page 114 and 115: 112 Conceptual model of the sources
Page 116 and 117: 114 3.8 Tributyltin (TBT) and the i
Page 118 and 119: 116 GES boundaries and matrix Exist
Page 120 and 121: 118 Monitoring the compound Status
Page 122 and 123: 120 Recommendation TBT measurements
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 150 and 151: 148 dead larvae can be induced by s
Page 152 and 153: 150 Strand, J, Dahllöf, I. (2005).
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
Page 170 and 171: 168 10. Spatial considerations Balt
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
Page 188 and 189: 186 4.19. Zooplankton species diver
Page 190 and 191: 188 indirectly impacted by eutrophi
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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196 4. Policy relevance Nonylphenol
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198 among different studies/measure
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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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