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Community Structure, Life Histories and Secondary Production of Stoneflies in Two Small Mountain Streams with Different Degree of Forest Cover

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Community Structure, Life Histories and Secondary Production of Stoneflies in Two Small Mountain Streams with Different Degree of Forest Cover J. Limnol., 2016; 75(1): 169-179 ORIGINAL ARTICLE DOI: 10.4081/jlimnol.2015.1262 Community structure, life histories and secondary production of stoneflies in two small mountain streams with different degree of forest cover Pavel BERACKO,* Andrea KUŠNÍROVÁ, Michaela PARTLOVÁ, Jana CICEKOVÁ Department of Ecology, Faculty of Natural Sciences, Comenius University, B-2 Mlynská Dolina, SK-842 15, Bratislava, Slovakia *Corresponding author: [email protected] ABSTRACT Our study examines community structure and nymphal biology (life cycles and secondary production) of stoneflies in two adjacent mountain streams with different degree of forest cover in the Prosiečanka River Basin (Chočské Vrchy Mts., West Carpathians). One of the streams has non-forested catchment, converted to meadows and pastures, while the other one has catchment with 60% covered by spruce forest. Differences in forest cover and in thermal regime of the streams were reflected by the difference of stonefly communities at their structural and functional level. Species Nemoura cinerea and Leuctra aurita created stonefly assemblage in non-forested stream, whereas Nemoura cinerea also occurred in naturally forested stream together with species Leuctra armata, Leuctra nigra, Leuctra prima, Siphonoperla neglecta and Arcynopteryx dichroa. All examined species had maximally annual life cycle and in eudominant species Nemoura cinerea one month shift was found in nymphal hatching and adult emergence betweenonly streams. Total secondary production of stoneflies in undisturbed stream (126.46 mg DW m–2 y–1) was more than two times higher than the production in non-forested stream (47.39 mg DW m–2 y–1). Key words: Deforestation; Plecoptera; life cycle; secondary production; smalluse stream. Received: May 2015. Accepted: October 2015. INTRODUCTION energy base of a stream (Kedzierski and Smock, 2001). A conceptual model assumes that the absence of riparian Macroinvertebrates are a key component of freshwater forest significantly increases the quantity of light striking food-webs, participating in matter and energy flow the stream channel and banks, affects the chemistry of through aquatic ecosystem (Covich et al., 1999; Wallace water flowing through the riparian zone towards the and Webster, 1996). The functional role of benthic popu- stream and reduces quantity of allochthonous material in lations in the trophic dynamics of any aquatic ecosystem the stream (Sweeney 1993, Cummins et al., 1989; Rowe reflects on one hand the individual and population attrib- and Richardson, 2001). These factors in turn affect the utes (life history, seasonal variation in density, biomass amount of primary production, the diversity of microhab- and production), and on the other hand the efficiency of itats, temperature and discharge regime, and availability trophic pathways i.e. how efficiently food materials are of particulate organic matter for primary consumers (Ly- passed along these pathwaysNon-commercial (Benke et al., 1992). The ford and Gregory, 1975; Towns, 1981; Tait et al., 1994; voltinism and the length of nymphal life in aquatic insects Cummins et al., 1989; Higler 1993). Finally, these factors are two most critical life history features necessary for the separately and in interaction may influence the functional understanding of their functional importance in streams. attributes of individual and population e.g. survivorship, In particular, these parameters are necessary for secondary growth, adults size and fecundity, timing of reproduction, production estimates, the development of energy budgets abundance, biomass, and, ultimately, the secondary pro- for stream, and for environmental impact assessment (Wa- duction of each species in the macroinvertebrates com- ters, 1979; Benke, 1984). Secondary production repre- munity (Sweeney, 1993). In particular, temperature sents a heterotrophic biomass formation and its regime and food resources are two of the most important measurement allows the evaluation of growth and bio- factors governing life history patterns, especially the in- mass turnover rates, which can improve understanding of dividual growth rate, seasonal timing of egg and nymphal the interspecific interactions inside the community and re- development and other life history attributes of aquatic lationships between benthic community and stream habi- insects (Lillehammer, 1975; Hawkins, 1986; Hauer and tat (Benke, 1993; Grubaugh et al., 1997; Huryn and Benke, 1987; Brittain and Sartori, 2009). On one hand, it Wallace, 2000; Woodcock and Huryn, 2007). Structural is essential to discuss the nutrition together with water and functional changes in macroinvertebrate community temperature. On the other hand, the quality and quantity are linked to the effect of the tree canopy removal on the of food resources are strongly linked to temperature (Van- 170 P. Beracko et al. note and Sweeney, 1980; Newbold et al., 1994). The in- the stream arising from catchment area deforestation can dividual growth rate of aquatic insects usually directly re- affect the structure and function of benthic communities, flects water temperature changes. The temperature the aim of the present study was to determine species influences the fecundity, egg incubation period, induction composition of stonefly assemblages, life history patterns and termination of diapause, duration and success of and secondary production of identified stonefly species in hatching, which all determine the patterns of distribution two contrasting streams regarding to the forest coverage and the competitive position of species in given habitat of their catchments. (Ward and Stanford, 1982). Temperature affects the nymphal life span, its duration being inversely propor- METHODS tional to the temperature in most cases (Humpesch, 1984). Study sites Riparian deforestation eliminates shading and can result in a 2-5°C warming of small streams, which is shown to The research was carried out in two second-order trib- greatly affect important life history characteristics of utaries in the upper stretch of Prosiečanka River Basin macroinvertebrates (Sweeney, 1993; Bilby and Ward, (Chočské Vrchy Mts., West Carpathians, Slovakia) (Fig. 1). 1991). Knowledge of life histories and emergence periods The geological substrate of both catchment areas is formed of aquatic insects (including stoneflies) is fundamental for by flysh. Although the streams are similar morphologically understanding species biology and behaviour, and also for (Tab. 1), they differ in the forest cover of their catchments. aquatic conservation purposes (Stazner and Resh, 1993). While the right tributary, site A (coordinates: N 49°10ʹ58.0ʹʹ, For example, this knowledge in a specific habitat can help to improve the use and interpretation of biotic indices only (Sheldon, 1999). Stonefly nymphs are conspicuous com- ponent and essential links in the food webs in running water ecosystems (Hynes, 1970; Stewart and Stark, 1993). Tab. 1. Abiotic usecharacteristics of the forested stream (site B) and Most stonefly species are stenothermic; consequently, deforested stream (site A). variations in thermal regime of watercourses can limit Site A Site B their distribution (Ward, 1985; Quinn and Hickey, 1990) Max. width (m) 2 2.8 and determine changes in their life history attributes (Brit- Max. depth (m) 0.25 0.32 tain, 1983; Brittain et al., 1984; Sweeney and Vannote, Slope (‰) 35 46 1986; Perry et al., 1987; Lillehammer et al., 1989; Li et Max. temperature (°C) 20.1 17.2 al., 2011; Bottová et al., 2013; Krno et al., 2013). In par- pH 7.8 8.1 ticular, the distributions and life histories of stoneflies can Conductivity (μS m–1) 440 260 3– –1 be strongly affected by riparian deforestation (O’Hop et PO4 (mg L ) 0.04 0.03 – –1 al., 1984; Quinn et al., 1997; Krno, 2000, Krno et al., NO3 (mg L ) <2.0 <2.0 2– –1 2013). Because the changes in abiotic characteristics of SO4 (mg L ) 3.8 13.3 Non-commercial Fig. 1. Map of the study area, showing its location in Slovakia. Black circles represent the position of the sampling sites. Forest cover as the determinant of species composition and nymphal biology of stoneflies 171 E 19°29ʹ36.9ʹʹ, 920 m asl) had 90% of the catchment defor- using the size-frequency method (Benke, 1979; Benke ested and converted to meadows and pastures, the left trib- and Huryn, 2006). Annual production of the rare species utary, site B (coordinates: N 49°11ʹ04.8ʹʹ, E 19°28ʹ58.0ʹʹ, was estimated by multiplying mean annual biomass by 920 m asl represented a well-preserved submountain stream annual P/B ratio calculated from an empirical equation with 60% of the catchment covered predominantly by developed for stonefly species (Leuctra nigra, Leuctra spruce forests. This fact was reflected in the different ther- prima, Siphonoperla neglecta) by Krno (1997), Krno and mal regime of both streams. The undisturbed site B had gen- Šporka (2003). Chi-square test was performed to test sta- erally lower temperature (mean temperature=9.7°C) and tistically significant differences in total density, biomass higher thermal fluctuations (CV=50%) than the disturbed and secondary production of stonefly assemblages be- site A (mean temperature=13.6°C, CV=37%). The average tween site A and site B. pair-wise temperature difference was 3.9°C. RESULTS Data collection and processing Biomass and secondary production Quantitative samples of the macrozoobenthos were col- lected monthly, from April to October 2005 using During the sampling period, a total of 7 species of Kubíček’s benthic sampler (area 0.1
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