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Conservation of Leafhoppers in Floodplain Grasslands – Trade-Off

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Conservation of Leafhoppers in Floodplain Grasslands – Trade-Off Journal of Insect Conservation (2005) 9:335–349 DOI 10.1007/s10841-005-0514-0 Ó Springer 2005 -1 Conservation of leafhoppers in floodplain grasslands – trade-off between diversity and naturalness in a northern German national park Judith Rothenbu¨ cher* and Matthias Schaefer Institute of Zoology, Ecology Group, Berliner Str. 28, 37073 Go¨ttingen, Germany; *Author for correspon- dence; (e-mail: [email protected]; phone: +0049-551-395529; fax: +0049-551-395448) Received 5 January 2005; accepted in revised form 17 June 2005 Key words: Auchenorrhyncha, Inundation, Lower Oder Valley National Park, Mowing, Wetland Abstract The impacts of mowing and of flooding on the leafhopper communities of a river flood plain were investigated. Samples were taken by a motor-driven suction apparatus. In 2001 leafhoppers were collected in a variety of sites differing in land use (fallows, mown sites) and in flood intensity (high, medium, low, none). In 2002 samples were only taken in fallows subject to different flooding regimes. In fallows, more species (43) were collected than in mown sites (33). Flooding had an effect only in fallows. Here, the most species-rich (29) communities occurred in sites not subject to flooding, whereas fewest species (21) were found in sites subject to regularly occurring long lasting winter floods. Mown sites were dominated by pioneer species. In fallows, the communities differed in respect to flood intensity. In fallows that were subject to summer and winter floods pioneer species prevailed. In contrast, in fallows that were flooded a long time during winter but not in summer, communities of very specialised species were found which were not very species-rich. For the conservation of the typical leafhopper communities of floodplain grassland, management by mowing should be at least reduced if not totally stopped and natural flooding dynamics should be restored. Introduction brates, harvestable or other economically selected taxa, and vascular plants (New 1999). It is widely The conservation of biotic communities and spe- assumed that preservation of invertebrates can be cies under preferably natural conditions to main- indirectly achieved through habitat conservation tain ecological stability and biological diversity is (Plachter 1994; New 1999). one of the main aims of national parks (IUCN In the present study planthoppers and leafhop- 1994; Bibelriether 1997). Insects are rarely at the pers (Hemiptera: Auchenorrhyncha; hereafter centre of conservation schemes, although they referred to simply as ‘leafhoppers’) were chosen as comprise – on a global scale – more than 50% of a model group to investigate the ways in which all described living species (Wilson 1992) and play conservation strategies carried out in a northern an important role in most terrestrial ecosystems German national park contribute to the preser- (Plachter 1994; New 1999). Furthermore, many vation of insects. Leafhoppers occur in high conservation strategies are based on, and their numbers of species and individuals in wet grass- implementation addresses, warm-blooded verte- land (Nickel and Achtziger 1999). Additionally, 336 they can easily be sampled and information on the conservation. Ecological restoration of large rivers ecology of most species is available in the literature should be (more) process-oriented instead of spe- which can be included for further analyses. cies-focused (Schiemer et al. 1999). Nickel and Habitat conservation management in grassland Hildebrandt (2003) stated that the responses of often includes regular cutting in order to prevent leafhoppers to mowing and flooding may be succession and brushwood encroachment (Cattin essentially similar in that a few generalist species et al. 2003), to maintain or achieve a high plant are selected and effects are difficult to disentangle diversity (e.g. Decleer 1990; Vercin et al. 2002; in field experiments. Therefore, they called for Cattin et al. 2003) or to preserve suitable habitats further investigations of the effect of flooding on for selected target species (e.g. Preiksa 1999; leafhoppers. Helmecke et al. 2003). Numerous studies investi- It was the aim of the present study to analyse the gating the impact of mowing on arthropods have impact of mowing and natural flooding on the been carried out in different types of grassland leafhopper community. On this basis, conclusions habitats (see Gerstmeier and Lang 1996). However, will be drawn about the limits and possibilities of conclusions about the effects of mowing on species conserving insect communities in restored flood- richness and diversity are incongruent. Gerstmeier plain grassland. and Lang (1996) differentiated between meadows of different moisture conditions and proposed habitat-specific management strategies. Thus, the Methods impact of mowing seems to depend on habitat conditions such as soil moisture or flooding impact. Study area Within the large amount of studies on the impact of mowing on leafhoppers, those carried out in tem- The study was carried out in the ‘‘Lower Oder porarily flooded habitats are scarce (e.g. Heller and Valley National Park’’ (Figure 1), which is the Irmler 1997; Nickel and Hildebrandt 2003). only floodplain national park in Germany. At The disturbance regime due to flooding, which present inundation of the floodplain is regulated. creates a diversity of successional stages across the In the so called ‘‘dry polder’’, dykes prevent riverine landscape, is a key factor for plants and inundation throughout the whole year. In the animals living in natural river floodplains. Thus, ‘‘wet polders’’, inundation is regulated by flood- the restoration of natural flooding conditions is gates, which are integrated into dykes along the another important focus of floodplain river. The gates are opened between November Figure 1. Location of the Lower Oder Valley National Park (Map design T. Rothenbu¨ cher). 337 and April each year, so the typical winter flood flood preceding the 2001 and 2002 growing sea- can inundate the floodplain. After closing the sons were estimated. The altitude of each study site floodgates to prevent inundation during spring was compared with the water level of the river and summer, the water is pumped out of the Oder at the nearest gauging station on a daily basis polders to make land use possible. Currently, during the time the floodgates were open. Periods changes in land use as well as the management of of summer flooding of the sites situated on the the flooding regime are being attempted. Con- river bank were recorded in the field. For the servation management for selected target species analyses, flood intensity was classified as follows such as the corncrake (Crex crex) is planned for (Figure 2): 50% of the area, which includes regular cutting of the floodplain meadows (IUS 1998). The • High flood intensity: These plots are situated on remaining area will be left for succession and a the narrow river bank between the dyke and the more natural flooding regime will be restored river and are inundated not only by the winter (IUS 1998). At present, about 10% of the na- floods (winter 2000/01: approximately 50 days; tional park area is declared as core zone. This winter 2001/02: approximately 100 days), but also area has been abandoned since 1995 and left for occasionally and unpredictably in summer after succession (Jehle and Pankoke 1999), however, heavy rainfall (summer 2001: approximately flooding is still regulated. Currently, the study 20 days; summer 2002: approximately 5 days). area consists of a mixture of sites differing in land Therefore, they are the most heavily disturbed sites use (i.e. sites mown twice a year, in late spring and their degree of naturalness is lowest. and late summer, and fallows) as well as in flood • Medium flood intensity: These sites are situated intensity. in ditches in the wet polder and are subject to regular flooding for a long time during winter (winter 2000/01 & 2001/02: approximately Study sites and sampling procedure 130 days). Flooding conditions in these sites are close to natural flooding conditions. Samples were taken by a motor driven suction apparatus four times between May and September 2001 and 2002, respectively. The samples were taken in study sites differing in land use and in flooding period and frequency (Table 1). Unfor- tunately, the study design became unbalanced due to changes in land use during the year 2001. All plots that are classified as ‘‘mown sites’’ were mown regularly twice a year during the years previous to the study and during sampling years. Precise data on winter flooding were not available Figure 2. Schematic cross section of the floodplain showing the because of non-accessibility of the area during the habitats studied (river bank, depressions in the polders, higher flooding period. The approximate number of days elevations in the polders) and the corresponding high, medium of inundation of the study sites during the winter and low flooding impact. Table 1. Study design. The number of study sites investigated is listed for each pair of influencing factors. Year Location River bank Wet polder Dry polder Time of flood Summer & winter Winter (long) Winter (short) No flood Flooding impact High Medium Low None 2001 Mown grassland 1 5 2 2 Fallows 2 2 5 1 2002 Fallows 3 3 3 3 338 • Low flood intensity: These sites are situated in The average degree of specialisation of Auc- more elevated locations in the wet polder and are henorrhyncha communities was calculated based subject to more unpredictable and short winter on individuals, using the specialisation factor of floods (winter 2000/01: approximately 80 days; each species: winter 2001/02: approximately 100 days). PS • No flooding: These plots are situated in the dry SFi  ni i¼1 polder and are not flooded throughout the whole DSI ¼ year. N where DSI is the degree of specialisation based on Reed grass (Phalaris arundinacea) is the domi- individuals, S the total number of species, SF the nating plant species in the study area.
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