Author: Echaniz, Santiago Andrés; Vignatti, Alicia María
Date published: July 1, 2011
Journal code: LAJA
Saline water bodies can be defined as those with salinities equal to or higher than 3 g L-1 (Hammer, 1986). They are widely distributed in the world and are abundant in arheic and endorheic basins of arid and semiarid regions (Williams, 2002). They are highly influenced by the human activities carried out in their basins, which cause changes in their characteristics, with the consequent loss of biodiversity (Velasco et al., 2006).
The limnology of water bodies in other latitudes is relatively well-known, whereas, in Argentina, there are only a few reports on the saline lakes of Buenos Aires (Olivier, 1955; Ringuelet, 1968, 1972) and Santa Fe provinces (José de Paggi & Paggi, 1998), the northwest (Locascio de Mitrovich et al., 2005; Villagra de Gamundi et al., 2008) and Córdoba province (Bucher, 2006). Therefore, the information on their taxonomic composition, abundance and zooplankton biomass and its variation is still scarce.
We have thus recently started studies on the ecology and zooplankton of saline lakes of La Pampa province, in the semiarid center of Argentina (Echaniz et al., 2005, 2006; Vignatti et al., 2007). However, in those works, we determined mainly the population density but not the biomass in relation with environmental parameters.
Many of the conclusions on the functioning of saline lakes are applicable for the shallow lakes of La Pampa, but little is known on the ecology of the assemblages recorded in the central region of Argentina, where some species, especially crustaceans, are endemic to the neotropical region (Adamowicz et al., 2004; Echaniz et al., 2005, 2006; Vignatti et al., 2007).
The aims of this work were to analyze the variations in the main limnological parameters and the zooplankton of an inorganic turbid shallow lake with high salinity, located in the north of La Pampa province, along its annual cycle, and to test the following hypotheses: i) that the high concentration of dissolved solids affects the taxonomic composition and abundance of the zooplankton community, ii) that inorganic turbidity has detrimental effects on the development of zooplankton (Quirós et al., 2002; Torremorell et al., 2007), and iii) that at nutrient concentrations equal to those of other Pampean water bodies with lower salinity, this lake has a higher biomass of zooplankton, in agreement with that reported by Evans et al. (1996) for lakes of Canada.
MATERIALS AND METHODS
The Prato shallow lake is located in the north of La Pampa province (64°15'W, 35°26'S) (Fig. 1), in a plain region with soft hills and covered with a sand layer of variable thickness (Calmels & Casadío, 2005), in the ecotone between the phytogeographical provinces of the Pampean Plains and the Thorny Forest (Cabrera, 1976). Has a surface of 62.8 ha and a maximum depth of 2.6 m.
The mean annual precipitations of the region are around 700 mm (Casagrande et al., 2006), with a maximum in summer, but the potential evapotranspiration is about 800 mm year-1 (Roberto et al., 1994). The lake is fed by rainfalls and, to a lesser extent, by phreatic waters. It is an arheic water body, which loses water by evaporation or infiltration and suffers large level fluctuations. The land of its basin is used for agriculture and extensive cattle breeding. It has a regular shape, its bottom sediments consists mainly of sands, and there is absence of macrophytes and ichtyc fauna.
Field and laboratory work
Samples were collected monthly from December 2005 until December 2006, except in August, in the three stations located along the longest axis of the lake.
Water temperature, dissolved oxygen concentration (oximeter Lutron® OD 5510), water transparency (Secchi disc), and pH (digital pH meter Cornning® PS 15) were determined in each station. Water samples were taken and kept refrigerated until their analysis in the laboratory.
Two quantitative zooplankton samples were collected in each site with a 10-l Schindler-Patalas trap, with a 0.04 mm mesh size, and one qualitative sample with a net 22 cm in diameter and a similar mesh size. All the samples were anesthetized with CO2 and kept refrigerated until fixation, with the aim to avoid contractions that may deform the individuals collected.
Salinity was determined by means of the gravimetric method with drying at 104°C. Chlorophyll-a concentration was measured by extraction with aqueous acetone and spectrophotometry (spectrophotometer Metrolab 1700) (Arar, 1997; APHA, 1999), total nitrogen by means of the Kjeldahl method, and total phosphorus by digestion with potassium peroxodisulfate in acid medium and UV-visible spectrophotometry (APHA, 1999).
The content of suspended solids was determined with fiberglass filters (Microclar FFG047WPH), dried at 103-105°C until constant weight and calcined at 550°C (EPA, 1993). Macro-and microzooplankton (Kalff, 2002) were counted under a stereoscopic and a conventional optical microscope, in Bogorov and Sedgwick-Rafter chambers respectively.
Conventional measurements of the individuals of each species sampled were taken with a Carl Zeiss ocular micrometer, and length-dry weight formulae were used to determine zooplankton biomass (Dumont et al., 1975; Rosen, 1981; McCauley, 1984; Culver et al., 1985; Kobayashi, 1997).
Non parametric ANOVA Kruskal Wallis test, Spearman's correlations and principal component analysis (PCA) (Zar, 1996; Mangeaud, 2004; Pérez, 2004) were carried out by means of the PAST software version 1.94b (Hammer et al., 2001).
Physical and chemical parameters
Spatial variations of this parameters were not significant, so we used mean values. The mean concentration of total dissolved solids in the water was 25.3 g L-1, but increased as the level of water decreased (Fig. 2 and Table 1), and was characterized by the predominance of Cl- and Na+, which were higher than 49% and 92% of the anions and cations respectively. The pH was high (9.02 ± 0.16) and relatively stable (Table 1).
The water temperature varied seasonally, with a maximum of 26.8°C in December 2005 and a minimum of 8.1°C in July 2006 (Fig. 3). The concentration of dissolved oxygen was also variable, oscillating between 9.8 mg L-1 in December 2005 and 1.3 mg L-1 in April 2006 (Fig. 3). The concentration of nutrients was high and variable (Table 1). Chlorophyll-a concentration correlated with water temperature (R = 0.73; P = 0.0065) and presented a maximum in February 2006, but was relatively low and stable during the rest of the period studied (Fig. 4).
The concentration of organic suspended solids was higher during the first four months and was significantly correlated with chlorophyll-a concentration (R = 0.65; P = 0.022), whereas that of inorganic suspended solids was more abundant during the last six months (Fig. 4). We found a significant correlation between the concentration of inorganic suspended solids and that of total phosphorus (R = 0.75; P = 0.005).
Water transparency was reduced (0.17 m ± 0.06) and variable along the year (Fig. 5, Table 1), and was significantly correlated with the concentration of inorganic suspended solids (R = -0.89; P = 0.0001), but not significantly correlated with that of organic suspended solids (R = 0.02; P = 0.940) or chlorophylla concentration (R = 0.40; P = 0.194) (Fig. 8).
We recorded a total of six species (Table 2). Among crustaceans, Moina eugeniae and the calanoid Boeckella poopoensis were constantly present, whereas M. macrocopa and the harpacticoid Cletocamptus deitersi were recorded along four and nine months respectively. Among rotifers, Brachionus plicatilis was present along 10 months, whereas B. dimidiatus along only 2 months (Table 2). Variations of micro- and macrozooplankton abundance between sampling sites were not significant.
The spatial variations of the zooplankton abundance and biomass were not significant, so we used mean values.
The density of the community presented two peaks during the warmer months (Fig. 6), produced mainly by rotifers (B. dimidiatus in January 2006 and B. plicatilis in December 2006). Although their abundance was very variable and there were months during which they were not recorded, they presented the highest annual mean abundance (Fig. 7, Table 2). The PCA, whose first two components allowed explaining more than 60% of the variance, showed positive correlations between their abundance, the concentrations of organic suspended solids, chlorophyll-a and water temperature, but negative correlations between their abundance and salinity and inorganic suspended solids concentrations (Fig. 8).
Among crustaceans, the most abundant species was B. poopoensis followed by M. eugeniae (Table 2). B. poopoensis presented its maximum abundances at the beginning of the summer, whereas M. eugeniae and M. macrocopa did so during fall. The PCA showed positive correlations between crustacean abundance, chlorophyll-a concentration and water transparency, but negative ones between crustacean abundance, salinity and inorganic suspended solids (Fig. 8).
The mean biomass of the zooplankton community (6614.1 ìg L-1 ± 4336.9) presented a peak during fall and a minimum in spring (Fig. 9). In all cases, the highest contribution was that of crustaceans (Fig. 10), among which B. poopoensis represented more than their biomass and salinity and organic suspended solid concentrations. The contribution of rotifers was important only in December 2006, when it represented 29.5% of the total (Fig. 10) and the PCA also showed a positive correlation with abundance and water temperature (Fig. 8).
The Prato lake is located in the western boundary of the Pampean plain (Cabrera, 1976), and although it shares characteristics with typical Pampean lakes of the province of Buenos Aires (Ringuelet, 1968 and 1972; Torremorell et al., 2007), such as the reduced depth and the polymixis, it differs from them because of its seasonality and great variations in water level and salinity.
These fluctuations are typical of most shallow lakes of La Pampa province, which are mainly fed by precipitations and lose water by evaporation (Echaniz et al., 2005, 2006; Vignatti et al., 2007). This phenomenon is particularly important because these lakes are located in a region where the evapotranspiration overpasses precipitations (Roberto et al., 1994). This characteristic was reflected in this lake by the decrease of almost 0.6 m in the water level and an increase in the concentration of dissolved solids, which, at the end of the study, was almost twice of the initial value, although it was within the mesosaline range (Hammer, 1986).
The absence of variations in the spatial distribution of physical and chemical parameters and zooplanktonic abundance and biomass of this lake was probably related to their shallow depth, the shape of their basin (flat and free from obstacles) and to wind action, all of which determine their polymictic condition and the permanent mixture of water.
Another feature shared by most lakes of La Pampa is the predominance of Cl- and Na+, with proportionally low bivalent cations concentrations (Ca++ and Mg++) (Echaniz et al., 2006).
The lake studied presented some characteristics that differentiate it from other environments of La Pampa with similar salinity, in particular, among the physical factors, its reduced transparency, which was almost 10 times lower than that recorded in previous studies (Echaniz et al., 2006; Vignatti et al., 2007). This high turbidity was due to the differential predominance of the two fractions of suspended solids along the year. Those of organic origin were higher during the summer, when the concentration of chlorophyll-a was also high, whereas those of inorganic origin were higher during winter and spring, when more intense winds are present (Cano, 1980). Due to the scarce depth of the lake, these winds cause the removal and resuspension of bottom sediments (Scheffer, 1998; Borell Lövstedt & Bengtsson, 2008). In addition, unlike that found in similar lakes of the province, this situation was favored by the total absence of macrophytes, which make resuspension more difficult.
The high concentrations of nutrients, which allowed us to characterize the lake as hypereutrophic (OECD, 1982), were similar to those of other environments of La Pampa (Echaniz et al., 2008; Echaniz & Vignatti, unpublished data), but, in particular, total phosphorus was several times higher than those reported by Quirós et al. (2002) and Sosnovsky & Quirós (2006) for shallow lakes of Buenos Aires province. This could be due, on one hand, to the high impact caused by the dragging of the feces of animals that feed on its basin, especially during storms (Carpenter et al., 1998; Bennett et al., 1999; Bremigan et al., 2008), since cattle can excrete between 9 and 16 kg of phosphorus.ind.year-1 (Russell et al., 2008). On the other hand, the resuspension of sediments by the wind is particularly important in shallow lakes (Markensten & Pierson, 2003; De Vicente et al., 2006; Borell-Lövstedt & Bengtsson, 2008), since removal favors the resolubilization of the nutrients of the internal load (Havens et al., 2007), which, in turn, favors the internal eutrophication of the lake (Smolders et al., 2006). This was probably the case in the lake studied in this work, since the highest concentrations of phosphorus were found during the second half of the year, during which stronger winds are present (Cano, 1980) and the concentrations of inorganic suspended solids were highest. In addition, the reduced capacity of phosphorus and nitrogen absorption of the sediments due to the relatively large size of the predominant particles (Kapanen, 2008) and to the fact that water is lost only by evaporation because the lake is an arheic environment leads to accumulation processes.
Zooplankton diversity was reduced, a common situation in environments with high salinity (Hammer, 1986; Herbst, 2001; Ivanova & Kazantseva, 2006), but another feature that differentiates this lake from others of La Pampa is the lower species richness found, since the species richness in other lakes with similar concentrations of dissolved solids but much higher transparency is close to 15 (Echaniz et al., 2006, Vignatti et al., 2007).
As regards the zooplankton found, the species recorded were typical of these ecosystems and were characterized by the presence of autochthonous halophilic crustaceans, such as Moina eugeniae, a species restricted to saline waters of the central region of Argentina (Paggi, 1998; Echaniz et al., 2006), and Boeckella poopoensis, a species that has a very wide geographical distribution, from the north of Patagonia to the south of Perú (Menu-Marque et al., 2000; De los Ríos, 2005; Locascio de Mitrovich et al., 2005). The two rotifer species found have a wide distribution and are tolerant to salinity (Fontaneto et al., 2006).
Other important differences found with other saline lakes of La Pampa were the high total mean abundance, which was between four and six times higher (Echaniz et al., 2006; Vignatti et al., 2007), and the numeric predominance of rotifers, which were almost four and ten times more abundant than copepods and cladocerans respectively, in spite of which their biomass was only about 7% of the total.
Among rotifers, B. plicatilis showed a more constant presence, since it was recorded during most of the year and its maximum density was several times higher than the maximum recorded in other lakes of the province (Echaniz et al., 2006).
The abundance and biomass of rotifers were affected by water temperature and chlorophyll-a concentration, but not by salinity or the concentration of inorganic suspended solids. In contrast, the abundance and biomass of both cladocerans and copepods were negatively affected by the concentration of inorganic suspended solids and salinity, but positively affected by water temperature, since both parameters were higher during summer and fall.
The zooplankton biomass of Prato shallow lake was two-fold higher than that recorded in the same period in Don Tomás and Bajo de Giuliani, two shallow lakes of La Pampa, which showed a similar concentration of nutrients, but salinities of 0.8 and 9.82 g L-1 and concentrations of chlorophyll-a of 154.6 and 173.7 mg m-3 respectively (Echaniz et al., 2008; Echaniz et al., 2009).
Besides, the macrozooplankton biomass of Prato lake was six times higher than the maximum determined by Quirós et al. (2002) in a group of 23 organic turbid shallow lakes of Buenos Aires, which presented salinities between 0.3 and 27 g L-1 and concentrations of chlorophyll-a of up to 405 mg m-3. This supports the hypothesis that although saline lakes have low concentrations of chlorophyll-a, lower algal biomass, and thus low primary productivity, they are able to support high zooplankton biomasses (Evans et al., 1996).
We thank the Facultad de Ciencias Exactas y Naturales, Universidad Nacional de La Pampa for the financial support of the project and Mr. Hugo Prato and his family, owners of the rural establishment in which the lake is located.
Adamowicz, S., P. Hebert & M.C. Marinone. 2004. Species diversity and endemism in the Daphnia of Argentina: a genetic investigation. Zool. J. Linn. Soc. Lon., 140(2): 171-205.
APHA. 1999. Standard methods for the examination of water and wastewater. American Public Health Association (APHA), American Water Works Association (AWWA) and Water Pollution Control Federation (WPCF), Washington, DC, 1268 pp.
Arar, E.J. 1997. In vitro determination of Chlorophylls-a, b, c + c and pheopigments in marine and freshwater algae by visible spectrophotometry. [http://www.epa. gov/microbes/m446_0.pdf]. Reviewed: 9 Ausgust 2010.
Bennett, E.M., T. Reed-Andersen, J. Houser, J. Gabriel & S. Carpenter. 1999. A phosphorus budget for the lake Mendota watershed. Ecosystems, 2: 69-75.
Borell-Lövstedt, C. & L. Bengtsson. 2008. The role of non-prevailing wind direction on resuspension and redistribution of sediments in a shallow lake. Aquat. Sci., 70: 304-313.
Bremigan, M., P. Soranno, M. González, D. Bunnell, K. Arend, W. Renwick, R. Stein & M. Vanni. 2008. Hydrogeomorphic features mediate the effects of land use/cover on reservoir productivity and food webs. Limnol. Oceanogr., 53(4): 1420-1433.
Bucher, E.H. (ed.). 2006. Bañados del río Dulce y laguna Mar Chiquita (Córdoba, Argentina). Academia Nacional de Ciencias, Córdoba, 215 pp.
Cabrera, A. 1976. Regiones fitogeográficas argentinas. Fascículo 1, Enciclopedia argentina de agricultura y jardinería. Ed. Acme, Buenos Aires, 85 pp.
Calmels, A. & S. Casadío. 2005. Compilación geológica de la provincia de La Pampa. Amerindia, Santa Rosa, 322 pp.
Cano, E. (coord.). 1980. Inventario integrado de los recursos naturales de la provincia de La Pampa. Instituto Nacional de Tecnología Agropecuaria (INTA), Provincia de La Pampa y Universidad Nacional de La Pampa, Buenos Aires, 493 pp.
Carpenter, S., N. Caraco, D. Correll, R. Howarth, A. Sharpley & V. Smith. 1998. Nonpoint pollution of surface waters with phosphorus and nitrogen. Ecol. Appl., 8(3): 559-568.
Casagrande, G.A., G.T. Vergara & Y. Bellini. 2006. Cartas agroclimáticas actuales de temperaturas, heladas y lluvias de la provincia de La Pampa. Rev. Fac. Agron., 17(1/2): 15-22.
Culver, D.A., M. Boucherle, D.J. Bean & J.W. Fletcher. 1985. Biomass of freshwater crustacean zooplankton from length-weight regressions. Can. J. Fish. Aquat. Sci., 42(8): 1380-1390.
De los Ríos, P. 2005. Richness and distribution of zooplanktonic crustacean species in Chilean altiplanic and southern Patagonia ponds. Pol. J. Environ. Stud., 14: 817-822.
De Vicente, I., V. Amores & L. Cruz-Pizarro. 2006. Inestability of shallow lakes: a matter of the complexity of factors involved in sediment and water interaction? Limnética, 251(1-2): 253-270.
Dumont, H.J., I. Van de Velde & S. Dumont. 1975. The dry weight estimate of biomass in a selection of Cladocera, Copepoda and Rotifera from the plankton, periphyton and benthos of continental waters. Oecology, 19: 75-97.
Echaniz, S., A. Vignatti & P. Bunino. 2008. El zooplancton de un lago somero hipereutrófico de la región central de Argentina. Cambios después de una década. Biota Neotrop., 8(4): 63-71.
Echaniz, S., A. Vignatti, J.C. Paggi & S. José de Paggi. 2005. Riqueza y composición del zooplancton de lagunas saladas de Argentina. Rev. FABICIB, 9: 25- 39.
Echaniz, S., A. Vignatti, S. José de Paggi, J. Paggi & A. Pilati. 2006. Zooplankton seasonal abundance of south American saline shallow lakes. Int. Rev. Hydrobiol., (91): 86-100.
Echaniz, S., A. Vignatti & G. Cabrera. 2009. Características limnológicas de una laguna turbia orgánica de la provincia de La Pampa variación estacional del zooplancton. Biol. Acuát., 26: 71-82.
EPA (Environment Protection Agency). 1993. ESS Method 340.2: total suspended solids, mass balance (Dried at 103-105°C), volatile suspended solids (Ignited at 550°C). http://www.epa.gov/glnpo/ lmmb/methods/methd340.pdf. Reviewed: 9 Ausgust 2010.
Evans, M.S., M.T. Arts & R.D. Robarts. 1996. Algal productivity, algal biomass, and zooplankton biomass in a phosphorus-rich saline lake: deviations from regression model predictions. Can. J. Fish. Aquat. Sci., 53: 1048-1060.
Fontaneto, D., W. de Smet & C. Ricci. 2006. Rotifers in saltwaters, re-evaluation of an inconspicuos taxon. J. Mar. Biol. Assoc. UK, 86: 623-656.
Hammer, U.T., D. Harper & P. Ryan. 2001. PAST: Paleontological statistics software package for education and data analysis. Palaeontol. Electron., 4(1): 9 pp.
Hammer, U.T. 1986. Saline lake ecosystems of the world. Monographiae Biologicae 59. Dr. W. Junk Publishers, Dordrecht, 616 pp.
Havens, K., K.-R. Jin, N. Iricanin & R. James. 2007. Phosphorus dynamics at multiple time scales in the pelagic zone of a large shallow lake in Florida. Hydrobiology, 581: 25-42.
Herbst, D.B. 2001. Gradients of salinity stress, environmental stability and water chemistry as a templet for defining habitat types and physiological strategies in inland salt waters. Hydrobiology, 466: 209-219.
Ivanova, M.B. & T.I. Kazantseva. 2006. Effect of water pH and total dissolved solids on the species diversity of pelagic zooplankton in lakes: A statistical analysis. Russ. J. Ecol., 37(4): 264-270.
José de Paggi, S. & J.C. Paggi. 1998. Zooplancton de ambientes acuáticos con diferentes estados tróficos y salinidad. Neotropica, 44(1): 95-106.
Kalff, J. 2002. Limnology. Inland water system. Prentice Hall, New Jersey, 592 pp.
Kapanen, G. 2008. Phosphorus fractionation in lake sediments. Estuar. J. Ecol., 57(4): 244-245.
Kobayashi, T. 1997. Associations between environmental variables and zooplankton body masses in a regulated Australian river. Mar. Freshw. Res., 48: 523-529.
Locascio de Mitrovich, C., A. Villagra de Gamundi, J. Juárez & M. Ceraolo. 2005. Características limnológicas y zooplancton de cinco lagunas de la Puna-Argentina. Ecol. Bol., 40(1): 10-24.
Mangeaud, A. 2004. La aplicación de técnicas de ordenación multivariadas en la entomología. Rev. Soc. Entomol. Arg., 63(3-4): 1-10.
Markensten, H. & D.C. Pierson. 2003. A dynamic model for flow and wind driven sediment resuspension in a shallow basin. Hydrobiology, 494: 305-311.
McCauley, E. 1984. The estimation of the abundance and biomass of zooplankton in samples. In: J. Downing & F. Rigler (eds.). A manual on methods for the assessment of secondary productivity in freshwaters. Blackwell Scientific Publications, Oxford, pp. 228- 265.
Menu-Marque, S., J. Morrone & C. Locascio de Mitrovich. 2000. Distributional patterns of the south American species of Boeckella (Copepoda: Centropagidae): a track analysis. J. Crust. Biol., 20(2): 262- 272.
OECD (Organization for Economic Cooperation and Development). 1982. Eutrophication of waters. Monitorring, assesment and control. Final Report, París, 154 pp.
Olivier, S.R. 1955. Contribution to the limnological knowledge of the Salada Grande lagoon. Proc. Int. Assoc. Limnol., 12: 302-308.
Paggi, J. 1998. Cladocera (Anomopoda y Ctenopoda). In: S. Coscarón & J. Morrone (eds.). Biodiversidad de artrópodos argentinos. Ediciones Sur, La Plata, pp. 507-518.
Pérez, C. 2004. Técnicas de análisis multivariante de datos. Pearson Educación, Madrid, 646 pp.
Quirós, R., A. Rennella, M. Boveri, J.J. Rosso & A. Sosnovsky. 2002. Factores que afectan la estructura y el funcionamiento de las lagunas pampeanas. Ecol. Austral, 12: 175-185.
Ringuelet, R.A. 1968. Tipología de las lagunas de la provincia de Buenos Aires. La limnología regional y los tipos lagunares. Physis, 28(76): 65-76.
Ringuelet, R.A. 1972. Ecología y biocenología del hábitat lagunar o lago de tercer orden de la región neotrópica templada (Pampasia Sudoriental de la Argentina). Physis, 31(82): 55-76.
Roberto, Z., G. Casagrande & E. Viglizzo. 1994. Lluvias en la Pampa Central. Tendencias y variaciones. Publicación N°12, Centro Regional La Pampa-San Luis, INTA. Buenos Aires, 25 pp.
Rosen, R.A. 1981. Length-dry weight relationships of some freshwaters zooplankton. J. Freshw. Ecol., 1: 225-229.
Russell, M., D. Weller, T. Jordan, K. Sigwart & K. Sullivan. 2008. Net anthropogenic phosphorus inputs: spatial and temporal variability in the Chesapeake Bay region. Biogeochemistry, 88(3): 285-304.
Scheffer, M. 1998. Ecology of shallow lakes. Chapman & Hall, London, 357 pp.
Smolders, A.J.P., L.P.M. Lamers, E.C.H.E.T. Lucassen, G. van der Velde & J.G.M. Roelofs. 2006. Internal eutrophication: How it works and what to do about it - a review. Chem. Ecol., 22(2): 93-111.
Sosnovsky, A. & R. Quirós. 2006. El estado trófico de pequeñas lagunas pampeanas, su relación con la hidrología y el uso de la tierra. Ecol. Austral, 16:115- 124.
Torremorell, A., J. Bustingorry, R. Escaray & H. Zagarese. 2007. Seasonal dynamics of a large, shallow lake, laguna Chascomús: The role of light limitation and other physical variables. Limnology, 37: 100-108.
Velasco, J., A. Millán, J. Hernández, C. Gutiérrez, P. Abellán, D. Sánchez & M. Ruiz. 2006. Response of biotic communities to salinity changes in a Mediterranean hypersaline stream. Saline Systems 2:12. [http://www.salinesystems.org/content/2/1/12]. Reviewed: 9 August 2010.
Vignatti, A., S. Echaniz & M. Martín. 2007. El zooplancton de lagos someros de diferente salinidad y estado trófico en la región semiárida pampeana (La Pampa, Argentina). Gayana, 71(1): 38-48.
Villagra de Gamundi, A., C. Locascio de Mitrovich, J. Juárez & G. Ferrer. 2008. Consideraciones sobre el zooplancton de las lagunas de Yala (Jujuy, Argentina). Ecol. Bol., 43(2) 1-16.
Williams, W.D. 2002. Environmental threats to salts lakes and the likely status of inland saline ecosystems 2025. Environ. Conserv., 29: 154-167.
Zar, J.H. 1996. Bioestatistical analysis. Prentice Hall, New Jersey, 988 pp.
Received: 10 August 2010; Accepted: 22 May 2011
Santiago Andrés Echaniz1 & Alicia María Vignatti1
1Facultad de Ciencias Exactas y Naturales, Universidad Nacional de La Pampa
Avenida Uruguay 151, 6300 Santa Rosa, Provincia de La Pampa, República Argentina
Corresponding author: Santiago Echaniz (firstname.lastname@example.org)