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Im Rahmen des durch die EU geförderten LIFE-Projekts „Lippeaue“ wurden
künstliche Binnendünen angelegt, die Standorte für an Trockenheit und Nährstoffarmut angepasste Pflanzenarten bieten können. Im Jahr 2012 wurde eine Erfolgskontrolle der Vegetationsentwicklung auf den in den Jahren 2008 und 2009 neu geschaffenen Binnendünen durchgeführt.
Die meisten der neu angelegten Dünen in der Lippeaue bei Hamm waren im Jahr 2012 durch Grünlandvegetation auf sandigen und schluffigen Böden gekennzeichnet. Die Gesamtstickstoff-, Humus- und Wassergehalte des Bodens lagen an der oberen Grenze des Bereiches, der für Magerrasenentwicklung günstig ist. Da sich keine Magerrasenbestände in der Nähe befinden, ist eine Etablierung von Magerrasen ohne die gezielte Übertragung von Mahd- oder Rechgut nicht zu erreichen. Die im LIFE-Projekt angelegten Dünen sind daher nur bedingt in einzelnen Fällen für die Magerrasenentwicklung geeignet.
Die ökologische Wertigkeit von Binnendünen ergibt sich aus ihrer Eigenschaft als vegetationsökologisch bedeutsamer Sonderstandort innerhalb des durch Feuchtigkeit geprägten ökosystemaren Wirkungsgefüges der Aue. Wo sich Weidengebüsche auf den Dünen ausbreiten, müssen die Ziele der Auwaldentwicklung durch Sukzession und der Entwicklung von Magerrasen auch durch stärkere Beweidung gegeneinander abgewogen werden.
After foundation of the Wadden Sea National Park, grazing and artificial drainage was ceased or reduced on large areas of the salt marshes at the Schleswig-Holstein mainland coast (Northern Germany). The effect of grazing cessation versus intensive and moderate grazing on vegetation diversity was studied on small (plant species richness on plots between 0.01 and 100 m2) and large scale (vegetation type richness per hectare) over 18 to 20 years by analysing data from long-term monitoring programs. Plant species richness and vegetation type richness increased strongly over time in all management regimes, because grazing-sensitive species increased first in ungrazed marshes and later dispersed to and established in intensively grazed marshes. Dominance of the tall, late-successional grass Elymus athericus on 7% to 52% of all moderately and ungrazed (primarily high marsh) plots led to a decrease in species richness. After 18 to 20 years, species richness was highest in moderately and intensively grazed high marshes. Differences were significant only on small plots of up to 4 m2. On the large scale, vegetation type richness in the low marsh was higher without grazing, while no differences were found in the high marsh. Our results indicate that grazing effects differ between spatial scales and that different spatial scales have to be considered for monitoring and evaluation of vegetation diversity in salt marshes. To conserve vegetation diversity on all scales, a large-scale mosaic of different management regimes should be maintained.
A floodplain-restoration project along the Danube between Neuburg and Ingolstadt (Germany) aims to bring back water and sediment dynamic to the floodplain. The accompanied long-term monitoring has to document the changes in biodiversity related to this new dynamics. Considerations on and results of the vegetation monitoring concept are documented in this paper. In a habitat rich ecosystem like a floodplain different habitats (alluvial forest, semi-aquatic/aquatic sites) have different demands on the sampling methods.
Therefore, different monitoring designs (preferential, random, systematic, stratified random and transect sampling) are discussed and tested for their use in different habitat types of the floodplain. A stratified random sampling is chosen for the alluvial forest stands, as it guarantees an equal distribution of the monitoring plots along the main driving factors, i.e. influence of water. The parameters distance to barrage, ecological flooding, height above thalweg and distance to the new floodplain river are used for stratifying and the plots are placed randomly into these strata, resulting in 117 permanent plots. Due to small changes at the semi-aquatic/aquatic sites a transect sampling was chosen. Further, a rough stratification (channel bed, river bank adjacent floodplain) was implemented, which was only possible after the start of the restoration project. To capture the small-scale changes due to the restoration measures on the vegetation, 99 additional plots completed the transect sampling. We conclude that hetereogenous study areas need different monitoring approaches, but, later on, a joint analysis must be possible.