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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.
Establishment of calcareous grassland on ex-arable fields by introducing target species is one of the most frequently used methods to restore the species assemblages of this highly endangered habitat type. The present study evaluates the long-term success of calcareous grassland restoration on former arable land in the vicinity of one of the oldest nature reserves in Bavaria, the “Garchinger Heide”. The restoration experiment combined different measures like topsoil removal, transfer of freshly cut seed-containing hay and additional sowing to the following variants in a 21-year experiment: (1) No topsoil removal, no hay transfer (control), (2) no topsoil removal with immediate hay transfer, (3) topsoil removal with immediate hay transfer and (4) topsoil removal with hay transfer 10 years after the start of restoration. Eleven Red List species which had not been transferred successfully were additionally sown after 9 to 19 years. Due to a limited availability of seeds, sowing of these species was mainly restricted to areas with topsoil removal, where better establishment was expected due to low vegetation cover. Five rare species with abundant seed production were also sown to plots without topsoil removal and hay transfer. The nature reserve served both as the donor area of the target species and as the reference to evaluate restoration success. Regarding aboveground biomass and total vegetation cover, greatest similarity to the donor site was observed on plots without topsoil removal. In contrast, the highest numbers of target species occurred on plots with topsoil removal, hay transfer and additional sowing. Similarity in species composition between restoration sites and the reference area increased over time, but species composition of restored sites did not fully reflect the reference after 21 years. One reason for the remaining dissimilarity was probably that topsoil removal favored stress tolerant species which were less common on the mature and more fine-grained soils of the nature reserve. Plots without topsoil removal still differed from the reference by their high vegetation cover and a significantly higher proportion of mesophytic grassland species. The study also showed that 19 Red List species were successfully established on the former arable fields, eight of them presumably by sowing. Nevertheless, various other rare species have not been observed yet. Results on functional traits characterizing environmental adaptation and reproduction also underlined the differences between restoration plots and the reference site. Our study presents a ʽdynamic restoration approachʼ where managers evaluated the original factorial treatments after a decade and modified them by additional treatments where development was sub-optimal. Such additional treatments may have confounded the experimental design, but from a management perspective proved to be a promising option to establish species rich grassland of high conservation value with a reasonable expenditure of time.
Aims
Understanding fine-grain diversity patterns across large spatial extents is fundamental for macroecological research and biodiversity conservation. Using the GrassPlot database, we provide benchmarks of fine-grain richness values of Palaearctic open habitats for vascular plants, bryophytes, lichens and complete vegetation (i.e., the sum of the former three groups).
Location
Palaearctic biogeographic realm.
Methods
We used 126,524 plots of eight standard grain sizes from the GrassPlot database: 0.0001, 0.001, 0.01, 0.1, 1, 10, 100 and 1,000 m2 and calculated the mean richness and standard deviations, as well as maximum, minimum, median, and first and third quartiles for each combination of grain size, taxonomic group, biome, region, vegetation type and phytosociological class.
Results
Patterns of plant diversity in vegetation types and biomes differ across grain sizes and taxonomic groups. Overall, secondary (mostly semi-natural) grasslands and natural grasslands are the richest vegetation type. The open-access file ”GrassPlot Diversity Benchmarks” and the web tool “GrassPlot Diversity Explorer” are now available online (https://edgg.org/databases/GrasslandDiversityExplorer) and provide more insights into species richness patterns in the Palaearctic open habitats.
Conclusions
The GrassPlot Diversity Benchmarks provide high-quality data on species richness in open habitat types across the Palaearctic. These benchmark data can be used in vegetation ecology, macroecology, biodiversity conservation and data quality checking. While the amount of data in the underlying GrassPlot database and their spatial coverage are smaller than in other extensive vegetation-plot databases, species recordings in GrassPlot are on average more complete, making it a valuable complementary data source in macroecology.
Von 2010 bis 2014 wurden im Rahmen
des Projekts „ProSaum“ Verfahren zur
Wiederansiedlung arten- und blütenreicher Säume und Feldraine mit gebietsheimischem Wildpflanzensaatgut entwickelt. Für die standortangepassten
Saatmischungen wurden einheimische
Pflanzenarten ausgewählt, die typisch für
alte artenreiche Feldraine und mesophile
Saumgesellschaften im Raum Osnabrück
sind. Die Ergebnisse eines Blockversuchs und weiterer Versuche auf Landschaftsebene zeigen, dass es möglich
ist, artenreiche Säume und Feldraine
durch Ansaat in Kombination mit sorgfältiger Bodenbearbeitung und Entwicklungspflege wiederherzustellen. Aus den
Ergebnissen werden Empfehlungen für
die Standortauswahl, Bodenbearbeitung,
Ansaat und Pflege abgeleitet.
During recent decades, many studies have shown that the successful restoration of species-rich grasslands is often seed-limited because of depleted seed banks and limited seed dispersal in modern fragmented landscapes. In Europe, commercial seed mixtures, which are widely used for restoration measures, mostly consist of species and varieties of non-local provenance. The regional biodiversity of a given landscape, however, can be preserved only when seeds or plants of local provenance are used in restoration projects. Furthermore, the transfer of suitable target species of local provenance can strongly enhance restoration success.
We review and evaluate the success of currently used near-natural methods for the introduction of target plant species (e.g. seeding of site-specific seed mixtures, transfer of fresh seed-containing hay, vacuum harvesting, transfer of turves or seed-containing soil) on restoration sites, ranging from dry and mesic meadows to floodplain grasslands and fens. Own data combined with literature findings show species establishment rates during the initial phase as well as the persistence of target species during long-term vegetation development on restoration sites.
In conclusion, our review indicates that seed limitation can be overcome successfully by most of the reviewed measures for species introduction. The establishment of species-rich grasslands is most successful when seeds, seed-containing plant material or soil are spread on bare soil of ex-arable fields after tilling or topsoil removal, or on raw soils, e.g. in mined areas. In species-poor grasslands without soil disturbance and on older ex-arable fields with dense weed vegetation, final transfer rates were the lowest. For future restoration projects, suitable measures have to be chosen carefully from case to case as they differ considerably in costs and logistic effort. Long-term prospects for restored grassland are especially good when management can be incorporated in agricultural systems.