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Diatom Assemblages and Water Quality Assessment in the Duero Basin (Nw Spain)

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Diatom Assemblages and Water Quality Assessment in the Duero Basin (Nw Spain) Belg. J. Bot. 141 (1) : 39-50 (2008) © 2008 Royal Botanical Society of Belgium DIATOM ASSEMBLAGES AND WATER QUALITY ASSESSMENT IN THE DUERO BASIN (NW SPAIN) S. BLANCO1,2,*, L. ECTOR2, V. HUCK2, O. MONNIER2, H.M. CAUCHIE2, L. HOFFMANN2 and E. BÉCARES1 1 Área de Ecología, Universidad de León, E-24071 León, Spain 2 Department of Environment and Agro-biotechnologies, Public Research Centre - Gabriel Lippmann, 41, rue du Brill, L-4422 Belvaux, Grand-Duchy of Luxembourg (* Author for correspondence; e-mail: [email protected]) Received 17 May 2007; accepted 9 October 2007. ABSTRACT. — In order to determine water quality status in the Duero basin (NW Spain), epilithic diatom samples were collected and analyzed in 137 stations in August 2004 following normalized standard protocols. The floristic particularities of the diatom assemblages in the basin are discussed. A total of 429 diatom taxa were identified in the basin and 90 taxa (21%) were new for the Iberian Peninsula. Especially noticeable was the presence of Achnanthidium rivulare, only known until now from North America. Ordination revealed the existence of five species assemblages related to the following environmental factors: 5-Day Biochemical 3- Oxygen Demand (BOD5), [PO4 ], and conductivity. Light and scanning electron microscopy micrographs are provided for some common, infrequent or exotic diatom species present in the Duero basin. Three diatom indices (Specific Pollution Index SPI, European Index CEC and Biological Diatom Index BDI) were applied. All of them correlated significantly with water physical and chemical variables, but SPI achieved the best correlations, and is therefore recommended as the reference diatom index for this Mediterranean basin. KEY WORDS. — Bacillariophyta, bioindicators, diatom indices, Mediterranean Basin, Pollution Sensivity Index, Water Framework Directive. INTRODUCTION Standardized phytobenthos-based monitoring networks are one of the targets of the Water Frame- During the past three decades diatoms have work Directive (WFD, EUROPEAN PARLIAMENT & been used worldwide to determine the ecological EUROPEAN COUNCIL 2000), a legislative set that quality of freshwaters (see e.g., WHITTON et al. aims at assessing and restoring the ecological status 1991, WHITTON & ROTT 1996, PRYGIEL et al. of inland water bodies throughout EU countries. 1999). Diatoms fulfill the requirements of good This ecological status is defined as a deviation indicator organisms in aquatic ecosystems. They measurement between the characteristic structure occur in a wide variety of environments and show of aquatic biota and the reference conditions of the a broad range of tolerance along several gradients same parameter. The reference conditions corre- of abiotic factors, while individual species have spond to a water system with no or minor anthro- specific water chemistry requirements (ROUND pogenic impacts (ECTOR & RIMET 2005). 1991). Finally, sampling and processing are rela- The use of benthic diatoms for biomonitor- tively simple and cost-effective. ing purposes usually implies the application of 40 BELGIAN JOURNAL OF BOTANY 141 diatom indices. Until now, several methods have Mediterranean streams, adressing the need for a been proposed, mainly based on the ZELINKA & careful development of data sets in order to MARVAN (1961) formula, i.e., assigning a pair of understand the processes that are structuring individual values (pollution tolerance and ste- diatom assemblages in these ecosystems. noecy degree) to a certain set of common taxa. This paper reports the first extensive diatom Among these, the Specific Pollution Index (SPI, survey carried out in the Duero basin (NW CEMAGREF 1982), the Biological Diatom Spain). We analyze the applicability of three Index (BDI, AFNOR 2000) and the European common diatom indices for the evaluation of Index (CEC, DESCY & COSTE 1991) have been water quality, thus providing a scientific basis for routinely applied for European streams. As these the implementation of the WFD in the Iberic- indices are based on diatom collections from rel- Macaronesian region. atively homogeneous watercourses in Central and Western Europe, problems may arise when applied elsewhere. Adding to the presumable bio- STUDY AREA geographical constraints in the species dataset, the ecological particularities of the study area, The Duero basin (97 290 km2) is the largest one such as those characteristic of the Mediterranean in the Iberian Peninsula and covers part of Spain and bioclimate, may introduce a source of bias in Portugal. This study was performed in the Spanish water quality estimation. Despite this, several area of the basin (78 952 km2), located in the north- authors have studied the applicability of diatom- west of Spain (Fig. 1). The drainage basin, crossed based methods for biomonitoring Iberian rivers. transversally by the Duero River (895 km), covers an GOMÀ et al. (2004, 2005), BLANCO et al. (2007) extensive plateau (~750 m a.s.l.) mostly formed by and OSCOZ et al. (2007) reported a good perform- Tertiary and Quaternary (alluvial or colluvial) materi- ance of the SPI index in both mountain and als, divided in two sub-systems: a) a western plain, plateau Spanish rivers. However, it failed to diag- basically constituted by Paleozoic granites, and b) the central and eastern sedimentary catchment area, com- nose the effects of oil-spillage pollution in a posed of calcareous and marly terrains, with several Mediterranean stream (DAMÁSIO et al. 2007). evaporitic inclusions. The surrounding mountains SABATER et al. (1987), LEIRA & SABATER (2005) consist of heterogeneous siliceous materials, except and TORNÉS et al. (2007) stressed the relevancy of for the limestones in the central part of the Cantabric physiographical factors in the distribution of Range. The largest part of this endorheic basin is diatom assemblages in some Pyrennean and located within the Mediterranean bioclimate, here Fig. 1. Geographical location of the Duero basin in Spain. WATER QUALITY IN THE DUERO BASIN USING DIATOMS 41 characterized by a strong continentality (air tempera- theoretical minimal and maximal water quality sta- ture ranging between -25ºC and 45ºC). Mean annual tuses, respectively. These values were classified in the precipitation is 620 mm, concentrated in autumn quality categories established by the WFD: bad = [1- and winter, while the potential evapotranspiration is 5[, poor = [5-9[, moderate = [9-13[, good = [13-17[, ~700 mm year-1. A network of 80 large reservoirs reg- and high quality = [17-20]. ulates the flow in the main streams of the Duero basin. The relationships between physical and chemical Main land uses are agriculture and stockbreeding, parameters, and diatom indices, were established by industrial activities being of less importance. Popula- calculating Pearson’s correlation coefficients. Data tion density is one of the lowest in Europe (26 hab-km-2); (except for pH) were previously log-transformed to fit however, its aquatic ecosystems have suffered his- normality. In order to identify the main diatom species torically intense anthropogenic impacts. A more assemblages according to their occurrence in the sam- detailed description of the study area is available in pling stations, an ordination dendrogram was per- GARCÍA & GONZÁLEZ (1986) and CEBALLOS et al. formed (Bray-Curtis similarity index, unweighted (2003). pair-grouping method, SNEATH & SOKAL 1973). Finally, the species data and the physical, chemical and physiographical parameters were related by MATERIAL AND METHODS means of a Canonical Correspondence Analysis (CCA) using CANOCO ver. 4.5 (TER BRAAK & ˇ The survey was conducted in August 2004 in 137 SMILAUER 2002). Variables with inflation factors over sites along the rivers of the Spanish side of the Duero 20 were excluded from the analysis. A forward selec- basin, randomly selected from the Water Quality Sur- tion method was used to identify the environmental veillance Network of the Duero Basin Water Agency variables that significantly explained variance in (CHD). Water physical and chemical parameters were species data (Monte Carlo test, 199 unrestricted per- analyzed according to APHA (1995) and provided by mutations). Statistical differences between the groups the CHD automatic water analysis stations in each formed in the CCA plots were assessed by means of site. Diatom samples were taken and processed fol- Analysis of Similarity (ANOSIM, CLARKE 1993). The lowing Spanish standards (AENOR 2004, 2005). last two analyses were performed upon a restricted list ≥ Epilithon was sampled on submerged stones in the of the most frequent taxa ( 10 % in abundance in the flow, euphotic zone of each stream, using a tooth- whole dataset). brush, and preserved in 4% v/v formaldehyde. Clean frustule suspensions were obtained by oxidizing organic matter with hot hydrogen peroxide 30% v/v. RESULTS Carbonate inclusions were removed adding a few drops of hydrochloric acid. Permanent microscopic WATER PHYSICAL AND CHEMICAL PARAMETERS slides were mounted using a refractive resin (Naphrax®). At least 400 valves were identified and Waters were circumneutral throughout the counted under 1000x light microscopy (Leica DM- whole catchment area (Table 1), with a certain RB). Taxonomy and nomenclature followed common tendency towards alkalinity in the northern reference works (KRAMMER & LANGE-BERTALOT ranges. The highest conductivity values corre- 1986-1991, LANGE-BERTALOT 1995-2007, 2000- spond to the chalky substrate rivers in the 2002). Diatom indices SPI, BDI
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