基于底栖无脊椎动物群落的爱沙尼亚沿海水质定义/Eesti Rannikumere Vee Kvaliteedi Klassipiiride Maaratlemine surselgrootute Alusel

J. Kotta, V. Lauringson, A. Kaasik, I. Kotta
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引用次数: 10

摘要

欧盟水框架指令旨在保护、加强和恢复所有地表水,最终目标是到2015年实现良好的地表水状态。为了实施该指令,所有成员国都必须评估其沿海地区的状况,并开发或使用现有的分类系统,以支持未来的监测。因此,分类将是指令实施的关键部分(欧洲委员会,2000年)。众所周知,水生生态系统是植物和动物的复杂混合物。水生系统可能以许多非常不同的方式对其物理、化学和生物环境的变化作出反应,因为这些组合通常包括具有广泛生理耐受性、摄食模式和营养相互作用的生物体(例如Bonsdorff & Pearson, 1999;Kotta et al., 2008)。这也是为什么植物和动物在不同地点之间很少相似的原因,它们与当时的物理、化学和生物环境的相互作用决定了它们对人为压力的反应(Kotta et al., 2007;Veber et al., 2009;Lauringson et al., 2012)。分类系统试图描述所有这些相互作用,并使用统计操作人为地将观察到的连续体划分为离散的类。虽然分类系统作为管理概念具有相当大的价值,但必须记住,它们充其量只是实际生态质量的近似值(例如Southworth等人,2004;Bolliger & Mladenoff, 2005)。在波罗的海东北部,恶劣的环境条件导致底栖物种数量很少(Bonsdorff & Pearson, 1999);然而,这些物种可以被认为对包括人为压力在内的各种干扰具有很强的耐受性(Kotta et al., 2007, 2009)。因此,将自所谓的前富营养化时代以来发生的自然变率与人为引起的变化区分开来成为最大的挑战。事实上,在富营养化前时期的底栖生物研究很少,而且往往由于缺乏定量估计而受到阻碍(另见Kotta & Kotta, 1995;Eriksson等人,1998;Kovtun et al., 2009)。由于缺乏全面的数据集,很难评估底栖生物生活与富营养化前时代相比恶化的程度。在这方面,a . Jarvekulg在爱沙尼亚海洋研究所中央数据库中的早期文献提供了一个独特的机会来比较过去50年来的底栖大型无脊椎动物群落,这些数据可用于记录底栖动物分类群的敏感性值,并定义底栖动物群落的高质量状态。为咸淡水条件开发的生物水质指标提出了河口质量悖论的问题,因为河口自然是高度紧张的环境,并栖息着耐压力的生物群(Dauvin, 2007;Elliott & Quintino, 2007),它必须应对高自然负荷的有机物和降低的盐度。最广泛使用的生物指数,如海洋生物指数(AMBI)和生物质量指数(BQI)是为海洋地区开发的,在一些情况下,它们在微咸水体中的使用被发现存在问题(Borja等人,2009;Munari & Mistri, 2010)。波罗的海的盐度从入口处超过25到最内端小于1不等,代表了底栖生物群落的主要大规模结构因素(Voipio, 1981)。盐度梯度导致在波罗的海盐分含量较高的南部使用Shannon多样性指数(H′)、AZTI的AMBI和BQI时出现问题(Zettler等人,2007),在盐分含量较低、物种非常稀少的海域使用AMBI时也遇到问题(例如Perus等人,2007)。在波罗的海,近年来已经测试了几种改进的生态质量评估方法(Perus等. ...)
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Defining the Coastal Water Quality in Estonia Based on Benthic Invertebrate communities/Eesti Rannikumere Vee Kvaliteedi Klassipiiride Maaratlemine Suurselgrootute Alusel
INTRODUCTION The European Union Water Framework Directive aims at protecting, enhancing, and restoring all bodies of surface water with the ultimate aim of achieving good surface water status by 2015. In order to implement the directive, all member states have to assess the status of their coastal areas and develop or use existing classification systems to support future monitoring. Consequently, classification will be a key part of the implementation of the Directive (European Commission, 2000). It is known that aquatic ecosystems are complex mixtures of plants and animals. Aquatic systems may respond to variations in their physical, chemical, and biological environments in many very different ways because these assemblages typically include organisms with a wide range of physiological tolerances, feeding modes, and trophic interactions (e.g. Bonsdorff & Pearson, 1999; Kotta et al., 2008). This is also the reason why plant and animal assemblages are rarely similar between sites, and their interactions with prevailing physical, chemical, and biological environments determine their responses to human-induced stresses (Kotta et al., 2007; Veber et al., 2009; Lauringson et al., 2012). Classification systems seek to describe all these interactions and artificially divide the observed continua into discrete classes using statistical manipulations. While classification systems have considerable value as management concepts, it has to be remembered that they are at best an approximation of actual ecological quality (e.g. Southworth et al., 2004; Bolliger & Mladenoff, 2005). In the northeastern Baltic Sea, harsh environmental conditions result in a low number of benthic species (Bonsdorff & Pearson, 1999); nevertheless, these species can be considered very tolerant to various disturbances including anthropogenic stresses (Kotta et al., 2007, 2009). Thus, it becomes of utmost challenge to separate natural variability from human-induced changes that have occurred since the so-called pre-eutrophication era. In fact, benthic studies in the pre-eutrophication era are rare and often hampered by the lack of quantitative estimates (see also Kotta & Kotta, 1995; Eriksson et al., 1998; Kovtun et al., 2009). The extent to which the benthic life has deteriorated compared with the pre-eutrophication era is difficult to assess given the lack of comprehensive data sets. In this respect, the earlier documentation by A. Jarvekulg in the Central Databases of the Estonian Marine Institute provides a unique opportunity to compare the benthic macroinvertebrate communities over the last 50 years, and these data can be used to record the sensitivity values of zoobenthic taxa as well as to define the high quality status for zoobenthic communities. Biological water quality indices developed for the brackish water conditions raise the issue of the Estuarine Quality Paradox, as estuaries are naturally highly stressed environments and inhabited by stress-tolerant biota (Dauvin, 2007; Elliott & Quintino, 2007) that has to cope with both high natural loads of organic matter and decreased salinity. The most widely used biotic indices such as Marine Biotic Index (AMBI) and biological quality index (BQI) were developed for marine areas, and their use in brackish waterbodies has been found problematic in several cases (Borja et al., 2009; Munari & Mistri, 2010). The salinity in the Baltic Sea ranges from over 25 in the entrance to less than 1 in the innermost ends and represents the main large-scale structuring factor for benthic communities (Voipio, 1981). The salinity gradient has caused problems in using the Shannon diversity index (H'), AZTI's AMBI, and BQI in the more saline southern part of the Baltic Sea (Zettler et al., 2007), and problems were also encountered in using the AMBI in the less saline, very species-poor part of the sea (e.g. Perus et al., 2007). In the Baltic Sea, several modified approaches have been tested for the ecological quality assessment in recent years (Perus et al. …
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