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Volume 2012, Article ID 818490, 10 pages
http://dx.doi.org/10.1155/2012/818490
Research Article

Gerris spinolae Lethierry and Severin (Hemiptera: Gerridae) and Brachydeutera longipes Hendel (Diptera: Ephydridae): Two Effective Insect Bioindicators to Monitor Pollution in Some Tropical Freshwater Ponds under Anthropogenic Stress

Insect Behavioural Ecology Laboratory, Centre of Advanced Study in Zoology, Banaras Hindu University, Varanasi 221 005, Uttar Pradesh, India

Received 30 July 2011; Accepted 29 October 2011

Academic Editor: Matilda Savopoulou-Soultani

Copyright © 2012 Arijit Pal et al. This is an open access article distributed under the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.

Abstract

The abundance patterns of two insects, Gerris spinolae and Brachydeutera longipes, were found to be affected by abiotic aquatic factors including free carbon dioxide, dissolved oxygen, BOD, and phosphate concentrations prevailing in four tropical freshwater ponds, three of which being anthropogenically stressed. Regression analysis between each individual-independent water quality variable and insect abundance demonstrated a significant positive correlation in each case between B. longipes abundance and BOD, phosphate, free CO2, and algae dry weight, while a significant negative correlation of each of these variables was found with Gerris spinolae abundance. Moreover, a significant negative correlation of B. longipes abundance was calculated with dissolved oxygen concentration, while G. spinolae abundance exhibited a positive correlation with the same. Thus, G. spinolae appears to be a pollution sensitive, effective bioindicator for healthy unpolluted ponds, while B. longipes has potential as a pollution-resistant insect species indicative of pollution occurrence.

1. Introduction

Freshwater bodies in urban ecosystems are under stress due to anthropogenic pressures. Pollution of inland water habitats, both lotic (running water) and lentic (lakes and ponds), impacts pollution of soil and ground water and thereby affects the essential basic (drinking water supply) and social requirements (aesthetic, religious, etc.) of human societies. Monitoring and maintaining the water quality of wetlands is also important since these recharge the groundwater and also affect the plant diversity in its vicinity. Environmental monitoring of inland freshwater bodies is an essential prerequisite for their management. Biological indication is, therefore, increasingly being advocated. Biological indication or bioindication is the process of using a species or group of species that readily reflects the abiotic and biotic states of an environment, represents the impact of environmental change on a habitat, community, or ecosystem, or is indicative of the diversity of a subset of taxa or of the entire diversity, within an area [1, 2]. Bioindicators or ecological indicators are taxa or groups of animals that show signs that they are affected by environmental pressures due to human activities or the destruction of the biotic system [3]. Bioindicators also provide information about the cumulative impact of the various pollutants in an ecosystem [1, 46]. An ideal taxon must respond predictably, in ways that are readily observed and quantified to environmental disturbance [7]. Aquatic bioindicators used so far are plants [810] including diatoms [4, 11]; vertebrates, mainly fish [5, 12, 13] and macroinvertebrates [1, 6, 7, 14, 15]. Among invertebrates, insects are good candidates [1621]. However, not all insects respond in a predictable manner to environmental pollution. Insects widely utilized as bioindicators include larval Chironomids (Diptera: Chironomiidae) [22] and water striders (Hemiptera: Gerridae), the latter being particularly well known for indicating heavy metal pollution, [18, 2326] which is also characterized by oxygen stress. Insects offer a number of advantages as bioindicators. These include the availability of a wide range of insects from various insect orders which (i) exhibit high sensitivity and the degree of sensitivity gives a series of choice of bioindicators depending upon the needed resolution, (ii) involve the entire trophic levels, thus ecosystems can be monitored from functional point of view, (iii) exhibit high fecundity, greater breeding potential reduces the chances of the potential bioindicator getting destroyed entirely from the ecosystem, and finally (iv) involve less ethical problems.

While some studies have been carried out on bioindicators of lotic ecosystems [19, 2729] studies of potential insect bioindicators of lentic ecosystems are scanty [30, 31], especially those of the tropical regions [15]. The present study focuses on assessing the potential of two insect species: the water strider, Gerris spinolae (Lethierry and Severin) and the shorefly, a semi-aquatic dipteran, Brachydeutera longipes (Hendel). Studies pertaining to the genus Brachydeutera are scanty although its occurrence is reported from lentic habitats [32]. While water striders, common in freshwater water bodies of temperate and tropical water bodies, are predaceous [33, 34], the genus, Brachydeutera, is documented to include species such as B. hebes, B. argentata, and B. neotropica the larval stages of which scavenge upon dead and decaying plant and animal tissues and also consume algae [32]. Since B. longipes is reported to be an algal feeder [35] and algal blooms are characteristic feature of polluted ponds, this species merits further investigation to examine its potential as a bioindicator. The impact of abiotic aquatic factors on the ecological response of the two focal insect species was investigated and the relationship between the abundance pattern of each species and the degree of pollution was determined.

2. Materials and Methods

2.1. Study Sites

The investigations were carried out from January to March, 2011 (3 months), in Varanasi, Uttar Pradesh, India. Four man-made ponds presently under anthropogenic stress were selected for the present study. While the pond located in the Botanical garden of Banaras Hindu University (not being under any anthropogenic stress) was considered as the control and the three ancient ponds, about 200 years old [36] under anthropogenic stress (due to human activities such as bathing, washing clothes, dumping organic wastes in the form of flowers, and so forth, in the ponds, particularly during religious ceremonies and festivals) located in a thickly populated urban ecosystem, were taken as the experimental.

The Kurukshetra (Krk), Sankuldhara (Skd), Durgakund (Dgk), and Botanical garden (Btg) ponds are located in Assi, Khojwa, Durgakund, and Banaras Hindu University Campus areas, respectively. All the ponds except Btg have 1-2 old temples around them. The dimensions of Krk pond are about 20 m × 25 m × 6 m. Its four banks are bounded by stone tiles from all around. Due to dense human inhabitation around it, there is heavy anthropogenic pressure on it. The dimensions of Skd pond are about 30 m × 30 m × 7 m. Its parapets are also bounded by stone tiles and, in addition it is surrounded by iron grid fencing. The dimensions of Dgk pond are about 40 m × 40 m × 10 m. Its parapets are also bounded by stone tiles and in addition, it is surrounded by an iron grid fencing. Human activities including occasional bathing, washing of clothes, and dumping of organic wastes in the form of flowers, and so forth during religious and social ceremonies occur in all these three ponds. The dimensions of Btg pond are about 10 m × 8 m × 2 m. It was constructed for the purpose of watering garden plants. It is free from all anthropogenic pressures.

2.2. Water Quality Assessment

Transparency was determined for each pond by using the Sechhi disc method while total solids were assessed by the standard dry weight method [37]. All the other physical and chemical parameters were monitored twice a week () at each study site. DO and BOD (5 days, 20°C) were determined by the modified Winkler’s method [37]. Free CO2 level was assessed by titrating the samples with 0.05 N NaOH solution in the presence of phenolphthalein indicator. Phosphate ion concentration was determined by the standard spectroscopic method [37].

2.3. Insect Diversity of the Ponds and Selection of Insect Species for Investigation of Aquatic Bioindicator Potential

The study revealed that each of the ponds supported a variety of aquatic insects from different orders, including water striders, back swimmers, water bugs (Order: Hemiptera), flies, mosquito larvae (Order: Diptera), and damselfly, dragonfly (Order: Odonata). Among these, two insect species, namely, Gerris spinolae, Lethierry and Severin, (Hemiptera: Gerridae; det. NPIB) RRS No. 1116-1117/11 and Brachydeutera longipes, Hendel (Diptera: Ephydridae; det. NPIB), and (RRS No. 1118-1124/11), were selected for further studies. These were identified by experts of the Network Project on Insect Biosystematics (NPIB), Division of Entomology, Indian Agricultural Research Institute, New Delhi. These two species were selected to study the impact of specific abiotic factors prevailing in the three anthropogenically stressed ponds, on the basis of the preliminary field observations regarding their differential habitat preferences.

2.4. Abundance of Adult Stages of the Two Insect Species: Gerris spinolae and Brachydeutera longipes

Insect abundance was monitored twice a week () per pond. Quadrat sampling was done from sixteen different sites of each pond (four sites per side per pond), quadrats per pond. The following formula was used to calculate the abundance:

2.5. Life Cycle of B. longipes

Brachydeutera longipes was cultured under laboratory conditions by carefully adding about 10 mg of fresh algae, Microcystis sp. (which was carefully layered on the water surface), to 1 liter pond water contained in a 5 liter glass jar (). Thereafter, 2 pairs of B. longipes were introduced in each jar. Small fractions of the algae were examined daily under the Stereobinocular microscope and the various life cycle stages and feeding behaviour of the larval stages were recorded.

2.6. Statistical Analysis

Variation in the abiotic factors, that is, temperature, pH, free CO2, dissolved oxygen (DO), biological oxygen demand (BOD), phosphate ion concentration, and a biotic factor-concentration (dry weight/m2) of the algae, Microcystis sp. in each of the four ponds was analysed by using one-way analysis of variance (ANOVA) followed by Dunnett’s post hoc test by using SPSS-PC software. Regression analysis for calculation of the correlation between the abundance of each of the two insect species, Brachydeutera longipes and Gerris spinolae with each of the above-mentioned seven water quality parameters considered individually in each case, was carried out by using SPSS-PC software.

3. Results

3.1. Life Cycle of B. longipes

Examination of the surface of the algal vegetation under laboratory conditions showed the presence of pale brown, cigar-shaped operculated eggs. Three larval instars were recorded, the duration of each stage was found to be approximately 2-3 days with that of the pupal stage being about 3-4 days. The larvae were observed to feed voraciously on Microcystis sp. Adults were recorded to have an approximate life span of 2-3 months.

3.2. Water Quality Assessment

A significant variation in water transparency was found in the four ponds: Btg pond (182.5 cm), Krk pond (63.8 cm), Skd pond (52.67 cm), and Dgk pond (29.67 cm). There was also variation in the amount of total solids present in each pond, with Btg pond having least amount of total solids including dissolved (275.8 mg/L) and suspended (3.9 mg/L) in comparison to the solids present in the other three ponds. The amount of dissolved solids were 321.7 mg/L, 537.2 mg/L, and 873.9 mg/L and suspended solids were 4.1 mg/L, 4.6 mg/L, 7.3 mg/L in Krk, Skd, and Dgk ponds, respectively (Figure 1).

818490.fig.001
Figure 1: Concentration (mg/L) of total solids, suspended solids and dissolved solids in the control (Botanical garden) and anthropogenically stressed (Kurukshetra, Sankuldhara and Durgakund) ponds.

Six abiotic parameters, namely, temperature, pH, free CO2, dissolved oxygen (DO), BOD, phosphate ion concentration, and one biotic parameter, that is, food availability of B. longipes larvae in terms of the dry weight of Microcystis sp. per square meter, were monitored in all the four ponds. Significant variation was found in case of each parameter except temperature, for all the four ponds: ANOVA-temperature ; ), pH (; ), free CO2 (; ), dissolved oxygen (; ), biological oxygen demand (; ), concentration of phosphates (; ), and food availability of B. longipes larvae in terms of dry weight of Microcystis sp. per square meter (; ) Table 1.

tab1
Table 1: Physical, chemical, and biological parameters of water quality in the four ponds (Botanical garden—control; Kurukshetra, Sankuldhara and Durgakund—anthropogenically stressed) located in different parts of Varanasi, India.

Post hoc tests revealed significant differences (Dunnett’s test, ) in case of each parameter under study (except free CO2 level which was not found to be significantly different ( in the Krk pond), in all the three experimental ponds in comparison to the control.

3.3. Abundance of Adult Stages of Insects, Gerris spinolae and Brachydeutera longipes, in the Four Ponds

The abundance of adult stages of Gerris spinolae and B. longipes in the four ponds varied significantly: one-way ANOVA: ; , for G. spinolae, and ; , for B. longipes (Figures 2(a) and 2(b)).

fig2
Figure 2: Abundance (No./sq. m) of adults of (a) Brachydeutera longipes (Hendel) and (b) Gerris spinolae (Lethierry and Severin) in the control (Botanical garden) and anthropogenically stressed (Kurukshetra, Sankuldhara and Durgakund) ponds, where *, **, and ***, ns—not significant.

Post hoc tests revealed significant differences in the abundance of B. longipes in all the three experimental ponds in comparison to the control pond, the lowest being in Dgk pond (Dunnett’s test, ), with abundance being in the increasing order in Skd and Krk ponds (Dunnett’s test, , for both). The two experimental ponds Dgk and Skd differed significantly from the control (post hoc test: Dunnett’s test, , for both) in exhibiting significantly lower abundance of the G. spinolae. However, Krk pond did not show significant deviation from the control pond in this respect (Dunnett’s test, ).

Regression analysis between each individual independent water quality variable: temperature, pH, BOD, DO, free CO2, phosphate, dry weight of algae, with the abundance of adult stage of each of the two insect species, Brachydeutera longipes and Gerris spinolae (dependent variables) reveals the following: a significant positive correlation () between B. longipes abundance and BOD (), PO4 (), free CO2 (), and dry weight of algae (.519) and a significant negative correlation () with DO (). On the other hand, G. spinolae abundance exhibited a significant positive correlation () with DO () and temperature () and a significant negative correlation () with BOD (), PO4 (), free CO2 (.829), and dry weight of algae () Table 2.

tab2
Table 2: Regression analysis output obtained by corelating each variable (water quality parameter) independently with the abundance of each of the two insect species, Brachydeutera longipes and Gerris spinolae.

Brachydeutera longipes abundance showed less significant positive correlation with pH (, ) and a negative correlation with temperature (, ) whereas G. spinolae abundance demonstrated no significant correlation with pH (, ) Figures 3(a), 3(b); 4(a), 4(b); 5(a), 5(b); 6(a), 6(b); 7(a), 7(b); 8(a), 8(b); and 9(a), 9(b).

fig3
Figure 3: Relation between BOD and abundance of (a) Brachydeutera longipes (Hendel) and (b) Gerris spinolae (Lethierry and Severin) as shown by regression analysis.
fig4
Figure 4: Relation between DO and abundance of (a) Brachydeutera longipes (Hendel) and (b) Gerris spinolae (Lethierry and Severin) as shown by regression analysis.
fig5
Figure 5: Relation between free carbon dioxide and abundance of (a) Brachydeutera longipes (Hendel) and (b) Gerris spinolae (Lethierry and Severin) as shown by regression analysis.
fig6
Figure 6: Relation between phosphate ion concentration and abundance of (a) Brachydeutera longipes (Hendel) and (b) Gerris spinolae (Lethierry and Severin) as shown by regression analysis.
fig7
Figure 7: Relation between dry weight of algae (g/sq. m) and abundance of (a) Brachydeutera longipes (Hendel) and (b) Gerris spinolae (Lethierry and Severin) as shown by regression analysis.
fig8
Figure 8: Relation between temperature of water and abundance of (a) Brachydeutera longipes (Hendel) and (b) Gerris spinolae (Lethierry and Severin) as shown by regression analysis.
fig9
Figure 9: Relation between pH of water and abundance of (a) Brachydeutera longipes (Hendel) and (b) Gerris spinolae (Lethierry and Severin) as shown by regression analysis.

4. Discussion

Our study clearly reveals that the abundance of adult stages of the two insect species, G. spinolae and B. longipes in the three ponds under anthropogenic stress is affected (although in a contrasting manner) due to differences in the levels of organic pollution and the resulting impacts of abiotic and biotic aquatic components of the ponds. Durgakund, Sankuldhara, and Kurukshetra ponds exhibit pollution in a decreasing order with higher concentrations of total dissolved and suspended solids, free CO2 levels, phosphate ion concentration, and amount of Microcystis sp. being more prevalent in the most polluted Durgakund pond and less in the remaining two anthropogenic stressed ponds. Temperature and pH were higher in the polluted ponds in comparison to the control while transparency was much reduced. Thus, the greater the pollution level in the pond, the lesser is the abundance of G. spinolae as demonstrated by its low abundance in the Durgakund pond. Regression analysis between each individual independent water quality parameter with the abundance of B. longipes revealed a significant positive impact of BOD, free CO2, phosphate concentration, and dry weight of algae (characteristic of polluted aquatic conditions) and a negative impact of DO concentrations. On the other hand, a significant positive influence of dissolved oxygen concentration (characteristic of unpolluted aquatic conditions) was found on G. spinolae abundance with the correlation being negative with BOD, free CO2, phosphate concentration, and dry weight of algae (characteristic of polluted aquatic conditions). Therefore, higher abundance of B. longipes appears to indicate greater aquatic pollution. Since the maintenance of integrity between the physico-chemical and biological components of an ecosystem determines its health status [5, 38], it is abundantly clear that G. spinolae prefers unpolluted, while the semiaquatic shore fly prefers polluted lotic water bodies.

Earlier studies demonstrate that physical, chemical, and biological parameters of an aquatic ecosystem are found to be correlated [39, 40]. Since each parameter in an aquatic ecosystem regulates the others, a freshwater pond supports complex dynamics. It has been reported that pH decreases with the increase in temperature [41]. Moreover, increasing turbidity of water increases heat retention capability of water [42]. Hence, ponds having turbid water exhibit relatively high temperature and slightly low pH as is evident in the Durgakund pond. Physical parameters also regulate the concentration of several ions, content of free CO2, dissolved oxygen, even BOD [43]. However, anthropogenic stress in the three experimental ponds is apparently due to the dumping of organic wastes [44]. Increasing organic degradation initially results in nutrient enrichment and finally in colonization of the various algae and “algal bloom” formation resulting in “eutrophication.” The extent of organic pollution in terms of increase in BOD, free CO2, and heavy oxygen stress can be monitored conveniently by using G. spinolae and B. longipes as bioindicators. The extent of pollution in ponds can be assessed by the abundance of B. longipes which may be predicted to increase and that of G. spinolae to decrease with increasing pollution levels. The reason behind the contradictory responses of the two insects under study is due to differences in the habitat requirements of their life-history stages. Gerris spinolae lays eggs on the submerged vegetation at depths of 2-3 meters from the surface [14]. This submerged oviposition is regulated by the level of dissolved oxygen and male presence [14]. After emergence, the nymphs respire using dissolved oxygen of the water, though the adults “skate” on the pond surface. This explains the negative correlation of their abundance with parameters indicative of higher level of pollution. Consequently, reduction in the abundance of G. spinolae may be a good indication of oxygen deficiency of water. Contrastingly, B. longipes does not rely on dissolved oxygen for respiration. The surface-living maggots feed on some species of algae like Microcystis sp., while the adults are free flying and are reported to feed on particles floating on the pond surface by rapidly extending and retracting their proboscis [32], so their number increases with eutrophication. The study clearly demonstrates that G. spinolae and B. longipes are good positive and negative indicator taxa for healthy fresh water ponds. We, therefore, conclude that occurrence of higher G. spinolae population level indicates a positive correlation with healthy unpolluted pond conditions while enhanced abundance of B. longipes indicates higher pollution level of the pond.

Since insects exhibit high fecundity, are fast breeding, easy to sample, and ethical constraints are not involved, Gerris spinolae (Lethierry and Severin) and Brachydeutera longipes (Hendel) appear to be suitable insect bioindicator candidates for assessing pollution in fresh water bodies. Utilisation of insect bioindicators would be an inexpensive method for monitoring pollution and for carrying out preliminary assessments of the water quality of inland ponds and lakes. This would avoid direct assessment of water quality involving expensive analytical methods, particularly at the preliminary stages. Integration of inexpensive biomonitoring methods with chemical-specific assessment methods would facilitate the restoration of the biological integrity and ecological health of freshwater bodies.

Acknowledgments

A. Pal and D. C. Sinha thank the Head of the Department of Zoology, Banaras Hindu University, for providing laboratory facilities for carrying out the research. The authors appreciate the advice of Dr. B. P. Singh and the help provided by Sudha Kumari for carrying out the statistical analysis. The authors also acknowledge the kind help of Dr. V. V. Ramamurthy, IARI, Pusa, New Delhi, India, for identification of the insect specimens.

References

  1. G. J. Niemi and M. E. McDonald, “Application of ecological indicators,” Annual Review of Ecology, Evolution, and Systematics, vol. 35, pp. 89–111, 2004. View at Publisher · View at Google Scholar · View at Scopus
  2. I. D. Hodkinson and J. K. Jackson, “Terrestrial and aquatic invertebrates as bioindicators for environmental monitoring, with particular reference to mountain ecosystems,” Environmental Management, vol. 35, no. 5, pp. 649–666, 2005. View at Publisher · View at Google Scholar · View at PubMed · View at Scopus
  3. B. McGeoch, “Biodiversity monitoring,” Annales Zoologici Fennici, vol. 37, pp. 307–317, 1998. View at Google Scholar
  4. T. Bere and J. G. Tundisi, “Biological monitoring of lotic ecosystems: the role of diatoms,” Brazilian Journal of Biology, vol. 70, no. 3, pp. 493–502, 2010. View at Google Scholar · View at Scopus
  5. J. R. Karr, “Assessment of biotic integrity using fish communities,” Fisheries, vol. 66, pp. 21–27, 1981. View at Google Scholar
  6. J. L. Metcalfe-Smith, “Biological water-quality assessment of rivers: use of macroinvertebrate communities,” The Rivers Handbook: Hydrological and Ecological Principles, vol. 2, pp. 234–246, 2009. View at Google Scholar
  7. R. Kopciuch, B. Berecka, J. Bartoszewicz, and B. Buszewski, “Some considerations about bioindicators in environmental monitoring,” Polish Journal of Environmental Studies, vol. 13, no. 5, pp. 453–462, 2004. View at Google Scholar · View at Scopus
  8. D. J. H. Phillips and P. S. Rainbow, “Biomonitoring of trace aquatic contaminants,” Journal of Applied Toxicology, vol. 14, pp. 315–316, 1993. View at Google Scholar
  9. L. V. Venkataraman, M. K. Krishi, and G. Suvarnalatha, “Algae as tool for biomonitoring and abatemnent of pesticide pollution in aquatic system,” Phykos, vol. 33, pp. 171–193, 1994. View at Google Scholar
  10. P. Chandra and S. Sinha, “Plant bioindicators of aquatic environment,” Millennium Issue, vol. 6, no. 1, 2000. View at Google Scholar
  11. B. K. Padhi, J. Rath, and P. K. Padhy, “Diatoms for assessing the ecological condition of inland freshwater bodies,” World Review of Science, Technology and Sustainable Development, vol. 7, no. 4, pp. 352–359, 2010. View at Publisher · View at Google Scholar · View at Scopus
  12. M. J. Vanni, C. D. Layne, and S. E. Arnott, “"Top-down" trophic interactions in lakes: effects of fish on nutrient dynamics,” Ecology, vol. 78, no. 1, pp. 1–20, 1997. View at Google Scholar · View at Scopus
  13. T. G. Northcote, “Fish in the structure and function of fresh-water ecosystems: a top- down view,” Canadian Journal of Fisheries and Aquatic Sciences, vol. 45, no. 2, pp. 361–379, 1988. View at Google Scholar · View at Scopus
  14. H. Hirayama and E. Kasuya, “Factors affecting submerged oviposition in a water strider: level of dissolved oxygen and male presence,” Animal Behaviour, vol. 76, no. 6, pp. 1919–1926, 2008. View at Publisher · View at Google Scholar · View at Scopus
  15. T. V. Ramachandra and M. Solanki, “Ecological assessment of lentic water bodies of Bangalore,” ENVIS Technical Report, vol. 25, pp. 1–105, 2007. View at Google Scholar
  16. A. Rayms-Keller, K. E. Olson, M. McGaw, C. Oray, J. O. Carlson, and B. J. Beaty, “Effect of heavy metals on Aedes aegypti (Diptera: Culicidae) larvae,” Ecotoxicology and Environmental Safety, vol. 39, no. 1, pp. 41–47, 1998. View at Publisher · View at Google Scholar · View at PubMed · View at Scopus
  17. D. Sánchez-Fernández, P. Abellán, A. Mellado, J. Velasco, and A. Millán, “Are water beetles good indicators of biodiversity in Mediterranean aquatic ecosystems? The case of the Segura river basin (SE Spain),” Biodiversity and Conservation, vol. 15, no. 14, pp. 4507–4520, 2006. View at Publisher · View at Google Scholar · View at Scopus
  18. M. Nummenlin, M. Lodineus, and E. Tulisalo, “Water strider as bioindicators of heavy metals,” Entomologica Fennica, vol. 8, pp. 185–191, 1998. View at Google Scholar
  19. M. Wayland and R. Crosley, “Selenium and other trace elements in aquatic insects in coal mine-affected streams in the Rocky Mountains of Alberta, Canada,” Archives of Environmental Contamination and Toxicology, vol. 50, no. 4, pp. 511–522, 2006. View at Publisher · View at Google Scholar · View at PubMed · View at Scopus
  20. Q. Zhou, J. Zhang, J. Fu, J. Shi, and G. Jiang, “Biomonitoring: an appealing tool for assessment of metal pollution in the aquatic ecosystem,” Analytica Chimica Acta, vol. 606, no. 2, pp. 135–150, 2008. View at Publisher · View at Google Scholar · View at PubMed · View at Scopus
  21. T. R. Lynch, C. J. Popp, and G. Z. Jacobi, “Aquatic insects as environmental monitors of trace metal contamination: Red River, New Mexico,” Water, Air, and Soil Pollution, vol. 42, no. 1-2, pp. 19–31, 1988. View at Google Scholar · View at Scopus
  22. D. S. Rao and A. B. Saxena, “Acute toxicity of mercury, zinc, lead, cadmium, manganese to the Chironomus Sp,” International Journal of Environmental Studies, vol. 16, no. 3-4, pp. 225–226, 1981. View at Google Scholar · View at Scopus
  23. L. Cheng, G. V. Alexander, and P. J. Franco, “Cadmium and other heavy metals in sea-skaters (Gerridae: Halobates, Rheumatobates),” Water, Air, and Soil Pollution, vol. 6, no. 1, pp. 33–38, 1976. View at Google Scholar
  24. L. Cheng, M. Schulz-Baldes, and C. S. Harrison, “Cadmium in ocean skaters, Halobates sericeus and in their sea bird predators,” Marine Biology, vol. 79, no. 3, pp. 321–324, 1984. View at Google Scholar · View at Scopus
  25. R. K. Bull, K. R. Murton, D. Osborn, P. Ward, and L. Cheng, “High levels of cadmium in Atlantic seabirds and sea-skaters,” Nature, vol. 269, no. 5628, pp. 507–509, 1977. View at Google Scholar · View at Scopus
  26. R. W. Clubb, R. A. Gaufin, and L.J. Lords, “Acute cadmium toxicity studies upon nine species of aquatic insects,” Environmental Research, vol. 11, pp. 355–368, 1975. View at Google Scholar
  27. D. F. Baptista, D. F. Buss, M. Egler, A. Giovanelli, M. P. Silveira, and J. L. Nessimian, “A multimetric index based on benthic macroinvertebrates for evaluation of Atlantic Forest streams at Rio de Janeiro State, Brazil,” Hydrobiologia, vol. 575, no. 1, pp. 83–94, 2007. View at Publisher · View at Google Scholar · View at Scopus
  28. D. J. Cain, S. N. Luoma, J. L. Carter, and S. V. Fend, “Aquatic insects as bioindicators of trace element contamination in cobble-bottom rivers and streams,” Canadian Journal of Fisheries and Aquatic Sciences, vol. 49, no. 10, pp. 2141–2154, 1992. View at Google Scholar · View at Scopus
  29. L. Li, B. Zheng, and L. Liu, “Biomonitoring and bioindicators used for river ecosystems: definitions, approaches and trends,” Procedia Environmental Sciences, vol. 2, pp. 1510–1524, 2010. View at Publisher · View at Google Scholar
  30. I. M. Schleiter, M. Obach, D. Borchardt, and H. Werner, “Bioindication of chemical and hydromorphological habitat characteristics with benthic macro-invertebrates based on Artificial Neural Networks,” Aquatic Ecology, vol. 35, no. 2, pp. 141–158, 2001. View at Publisher · View at Google Scholar · View at Scopus
  31. N. Menetrey, B. Oertli, M. Sartori, A. Wagner, and J. B. Lachavanne, “Eutrophication: are mayflies (Ephemeroptera) good bioindicators for ponds?” Hydrobiologia, vol. 597, no. 1, pp. 125–135, 2008. View at Publisher · View at Google Scholar · View at Scopus
  32. J. B. Keiper and W. E. Walton, “Biology and immature stages of Brachydeutera sturtevanti (Diptera: Ephydridae), a hyponeustic generalist,” Annals of the Entomological Society of America, vol. 93, no. 3, pp. 468–475, 2000. View at Google Scholar · View at Scopus
  33. T. Ambrose, T. Mani, S. Vincent, L. C. Kumar, and K. T. Mathews, “Biocontrol efficacy of Gerris (A) spinolae, Laccotrephes griseus and Gambusia affinis on larval mosquitoes,” Indian Journal of Malariology, vol. 30, no. 4, pp. 187–192, 1993. View at Google Scholar · View at Scopus
  34. J. R. Spence and N. M. Andersen, “Biology of water striders: interactions between systematics and ecology,” Annual Review of Entomology, vol. 39, pp. 101–128, 1994. View at Google Scholar · View at Scopus
  35. M. G. Venkatesh, M. D. Parthasarthy, and G. P.C. Basavanna, “Food and feeding behaviour of the shore-fly maggot, Brachydeutera longipes Hendel (Diptera: Ephydridae),” Indian Journal of Behaviour, vol. 1, pp. 10–13, 1977. View at Google Scholar
  36. http://www.indianetzone.com/14/durga_temple.htm. Downloaded on June 6, 2011.
  37. B. D. Tripathi and S. R. Govil, Water Pollution : An Experimental Approach, CBS Publishers, Delhi, India, 2001.
  38. M. Sengupta and R. Dalwani, “A biomonitoring of planktons to assess the water quality in the lakes of Nagpur,” in Proceedings of the Taal, World Lake Conference, pp. 160–164, 2007.
  39. A. A. Ansari and F. A. Khan, “Remediation of eutrophied water using Spirodela polyrrhiza L. Shleid in controlled environment,” Pan-American Journal of Aquatic Sciences, vol. 4, no. 1, pp. 52–54, 2009. View at Google Scholar · View at Scopus
  40. G. X. Wang, L. M. Zhang, H. Chua, X. D. Li, M. F. Xia, and P. M. Pu, “A mosaic community of macrophytes for the ecological remediation of eutrophic shallow lakes,” Wetland Restoration and Ecological Engineering, vol. 35, no. 4, pp. 582–590, 2009. View at Publisher · View at Google Scholar · View at Scopus
  41. Y. Chen and S. L. Brantley, “Temperature- and pH-dependence of albite dissolution rate at acid pH,” Chemical Geology, vol. 135, no. 3-4, pp. 275–290, 1997. View at Google Scholar · View at Scopus
  42. K. P. Paaijmans, W. Takken, A. K. Githeko, and A. F. G. Jacobs, “The effect of water turbidity on the near-surface water temperature of larval habitats of the malaria mosquito Anopheles gambiae,” International Journal of Biometeorology, vol. 52, no. 8, pp. 747–753, 2008. View at Publisher · View at Google Scholar · View at PubMed · View at Scopus
  43. W. J. S. Mwegoha, M. E. Kaseva, and S. M. M. Sabai, “Mathematical modeling of dissolved oxygen in fish ponds,” African Journal of Environmental Science and Technology, vol. 4, pp. 625–638, 2010. View at Google Scholar
  44. A. K. Gupta, K. Mishra, P. Kumar, C. Singh, and S. Srivastava, “Impact of religious activities on the water characteristics of prominent ponds at Varanasi (U.P.), India,” Plant Archives, vol. 11, no. 1, pp. 297–300, 2011. View at Google Scholar