Biomonitoring of heavy metal availability in the marine environment

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Abstract

Biomonitors can be used to establish geographical and/or temporal variations in the bioavailabilities of heavy metals in the marine environment, offering time-integrated measures of those portions of the total ambient metal load that are of direct ecotoxicological relevance. Heavy metal biomonitors need to conform to certain required characteristics, not least being metal accumulators. Use of a suite of biomonitors allows recognition of the presence and relative magnitude of different metal sources. For example, a macrophytic alga responds essentially to dissolved metal sources only, a suspension feeder like a mussel responds to metal sources in dissolved and suspended phases, and a deposit feeder responds to metal available in the sediment. Examples are given of suitable heavy metal biomonitors in the coastal waters of Europe, New Zealand, Hong Kong and China. It is not valid to compare absolute accumulated metal concentrations in biomonitors interspecifically, although interspecific comparisions of rank orders do allow cross correlations of relative bioavailabilities of heavy metals to different biomonitors at the same sites. There is a need to identify widespread cosmopolitan biomonitors to allow intra-specific comparisons of bioavailabilities between geographical areas. Such cosmopolitan biomonitors may include the alga Ulva lactuca, mussels of the genera Mytilus and Perna, the oysters Ostrea and Crassostrea, barnacles like Balanus amphitrite and Tetraclita squamosa, and the talitrid amphipod Platorchestia platensis. A major caveat in the use of such cosmopolitan biomonitors remains the need for reliable, specific taxonomic identification. © 1995.

Figures

  • Fig. 1 The global geographical distributions of the three riving species of Perna, P. canaliculus, P. perna and P. viridis. After Siddall (1980).
  • TABLE 1 Zinc concentrations (~tg g- 1) and 95% confidence limits (CL) in the mussel Perna viridis (means in whole soft tissues) and in the barnacle Balanus amphitrite (concentration in 0.004 g body as estimated from double log regression of Zn concentration against body weight) collected from 10 sites in Hong Kong, 1986. Mussels sharing the same letter in the ANOVA column and barnacles sharing the same letter in the ANCOVA column have metal concentrations not differing significantly at p>0.05. After Phillips & Rainbow (1988).
  • TABLE 2 Copper concentrations (~tg g-i) with 95% confidence limits (CL) in amphipods of 0.01 g standardized dry weight as derived from best-fit double log regressions. Amphipods were collected from sites near Dunedin, New Zealand. Samples of one species sharing any common letter in the ANCOVA column are not significantly different at p>0.05. After Rainbow et al. (1993a).
  • TABLE 3 Copper and zinc concentrations (lag g-l) with 95% confidence limits (CL) in talitroidean amphipods of 0.01 g standardized dry weight as derived from best-fit double log regressions. Amphipods were collected from the Isle of Cumbrae, Scotland, in September 1986. After Moore & Rainbow (1987).
  • Fig. 2 The global geographical distribution of the talitrid amphipod Platorchestia platensis. After Chevreux & Fage (1925), Rainbow & Phillips (1993).

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CITATION STYLE

APA

Rainbow, P. S. (1995). Biomonitoring of heavy metal availability in the marine environment. Marine Pollution Bulletin, 31(4–12), 183–192. https://doi.org/10.1016/0025-326X(95)00116-5

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