Nomenclature: Wisskirchen & Haeupler (1998).
Nine years of vegetation development in a postmining site: effects of spontaneous and assisted site recovery
Article first published online: 18 NOV 2011
© 2011 The Authors. Journal of Applied Ecology © 2011 British Ecological Society
Journal of Applied Ecology
Volume 49, Issue 1, pages 251–260, February 2012
How to Cite
Baasch, A., Kirmer, A. and Tischew, S. (2012), Nine years of vegetation development in a postmining site: effects of spontaneous and assisted site recovery. Journal of Applied Ecology, 49: 251–260. doi: 10.1111/j.1365-2664.2011.02086.x
- Issue published online: 17 JAN 2012
- Article first published online: 18 NOV 2011
- Received 15 March 2011; accepted 7 October 2011 Handling Editor: Jan leps
- Calamagrostis epigejos;
- ecological restoration;
- erosion control;
- hay transfer;
- mulch seeding;
- species introduction;
- Top of page
- Materials and methods
- Supporting Information
1. Highly disturbed areas such as surface-mined land provide a great challenge for ecological restoration. The goal is to identify appropriate restoration approaches in a continuum between technical reclamation and spontaneous succession. In particular, on slopes endangered by erosion, appropriate methods are needed that quickly establish vegetation cover but also take into account the natural potentials of the site.
2. In the mined area Roßbach (Saxony-Anhalt, Germany), we evaluated the effects of spontaneous succession and assisted site recovery (species introduction through hay transfer and sowing) during a 9-year experiment. We asked how rates and pathways of vegetation development differ between treatments and whether species composition converges over time owing to species exchange.
3. The application of green hay as well as the sowing of regional seed mixtures clearly accelerated vegetation development and led to the rapid establishment of species-rich grasslands. Hay transfer was most successful owing to the high amount of transferable target species. Moreover, both treatments facilitated the establishment of cryptogams and provided effective erosion control. Also, hay transfer and sowing clearly affected the pathway of succession. Calamagrostis epigejos migrated from nearby source populations and became increasingly dominant at sites with spontaneous succession. In contrast, the species-rich grasslands established after hay transfer and sowing were highly resistant to invasion of Calamagrostis and other ruderals.
4. Species exchange between treatments led to increasing similarity in vegetation composition over time. Nine years after implementation of the experiment, we did not find any significant differences between treatments in terms of total vegetation cover, species richness and the number of target species. However, the dominance ratio between target and nontarget species differed significantly. Species introduction through hay transfer and sowing led to a permanently higher abundance of grassland species and a lower coverage of ruderals compared with spontaneously developed sites. Hence, our results highlight the importance of initial floristic composition and the order of species arrivals for long-term vegetation development.
5. Synthesis and applications. Hay transfer and sowing of regional seed mixtures are appropriate restoration tools to achieve rapid revegetation when no potential seed sources of target species are available nearby or there are undesirable species that need to be suppressed. Our results show that introduced grassland species are able to grow under postmining site conditions and can migrate into adjacent spontaneously developing sites. A combination of spontaneous and assisted site recovery can promote the development of species-rich grasslands in postmining landscapes.
- Top of page
- Materials and methods
- Supporting Information
Ecological restoration of highly disturbed areas often aims to accelerate and/or manipulate vegetation development, thus is intrinsically linked to succession (e.g. Walker, Walker & del Moral 2007; Prach & Hobbs 2008; Walker & del Moral 2009). During the last few decades, spontaneous and assisted site recovery has been studied in postmining landscapes in Eastern Germany (e.g. Felinks, Pilarski & Wiegleb 1998; Kirmer & Mahn 2001; Wiegleb & Felinks 2001a,b; Kirmer et al. 2008; Baasch, Tischew & Bruelheide 2009). Several studies have shown that nutrient-deficient sites in mined areas can enhance biodiversity and provide habitats for rare species and plant communities. Therefore, one method of restoring surface-mined land could be through spontaneous succession (e.g. Prach & Pyšek 2001; Prach 2003; Tischew & Kirmer 2007). However, assisted site recovery is more appropriate on sites endangered by erosion, where managers seek to reintroduce species with low dispersal abilities or when ‘problematic’ species are nearby. Appropriate methods are those that quickly establish vegetation cover to provide basic ecosystem services in a short time (e.g. erosion control) (Norris et al. 2008). For this purpose, technical reclamation is predominantly used, i.e. ameliorating nutrient-poor substrates and sowing low-diversity mixtures of grass cultivars (Tischew & Kirmer 2007). There is much evidence that these measures often destroy the natural potential of the sites, thereby counteracting the development of biological diversity on marginal land (e.g. Mudrák, Frouz & Velichová 2010; Tropek et al. 2010). Therefore, conservationists and ecologists call for restoration strategies that include the natural potential of the sites and result in the development of species-rich vegetation of high nature conservation value (e.g. Tischew & Kirmer 2007; Řehounková & Prach 2008; Tropek et al. 2010). This might be achieved through the creation of species-rich grasslands using alternative restoration methods, e.g. hay transfer to accelerate and direct vegetation development. During the last few decades, land use changes in Europe have led to a continuous decline in the area of semi-natural grassland rich in biodiversity (e.g. EU 2010 Biodiversity Baseline Report; WallisDeVries, Poschlod & Willems 2002; Cremene et al. 2005; Pärtel et al. 2005; Krauss et al. 2010). In the face of increasing pressures on productive sites, the restoration of species-rich grasslands should be given higher priority in restoration schemes for marginal land such as nutrient-deficient mined sites.
In the mined area Roßbach, we investigated the success of three approaches to restoration: (i) application of fresh, diaspore-rich green hay, (ii) sowing of autochthonous species with an additional mulch layer and (iii) spontaneous succession to initiate vegetation development on unvegetated slopes. The experiment was established in the vicinity of small patches of dry grassland and stands dominated by Calamagrostis epigejos. This strong, competitive, clonal grass is widely seen as a ‘problem’ species in the conservation of grasslands (e.g. Rebele & Lehmann 2001; Fiala et al. 2004; Somodi, Virágh & Podani 2008) and for vegetation restoration in postmining landscapes in Central Europe (e.g. Prach & Pyšek 2001; Wiegleb & Felinks 2001a; Tischew & Kirmer 2007).
We hypothesized that the input of appropriate seeds via green hay and sowing would accelerate vegetation development leading to species-rich grassland communities within a few years, while revegetation through spontaneous succession would take longer and might lead to grasslands dominated by stands of Calamagrostis (Hypothesis 1). As in many restoration studies, it was not practical to weed the experimental site, thus treatments in the same locality should influence one another in the long term owing to species exchange (e.g. Bullock, Pywell & Walker 2007; Jongepierová, Mitchley & Tzanopoulos 2007; Lepšet al. 2007; Rydgren et al. 2010). Even so, we assumed that different rates and pathways of vegetation development on sites with and without species introduction will have a long-term influence on the composition of communities (Hypothesis 2), as species introduction will influence seed availability and dispersal stochasticity (e.g. Zobel et al. 2000), initial floristic composition (Egler 1954) and the sequence of species arrivals (e.g. Drake 1991). Long-term studies comparing different ecological restoration methods are rare for mining areas (see Kiehl et al. 2010). Our experiment evaluates the long-term effects of different methods to produce management recommendations for ecological restoration.
Materials and methods
- Top of page
- Materials and methods
- Supporting Information
Study Site and Sampling Design
The mined site Roßbach is part of the Geiseltal lignite mining district in Saxony-Anhalt (Germany). Our study area was situated in the southern part of the mined site and covered an area of 2·3 km2 (Kirmer et al. 2008). We set up an experiment in the centre of the study area on an artificial unvegetated slope with an inclination of c. 8°, an eastern aspect, and an altitude of c. 123 m a.s.l. (11°54′5·46′′E, 51°14′27·98′′N). In August 2000, the slope was shaped within the scope of remediation measures. The substrate consisted of dumped loess with a pH value (CaCl2) of 7·5. The material came from deeper soil layers, thus representing the features of primary succession (no soil development, no soil seed bank). In early September 2000, the experiment was established in a complete block design with three blocks and three treatments. (i) Sowing – S: 15 herbs and six grasses were sown at a density of 2 g/m2 or 860 seeds/m2 (site-specific seed mixture of autochthonous species, see Appendix S1, Supporting Information). Species were selected based on their ability to grow on dry, sunny sites (dry and mesic grassland species), satisfy aesthetic demands, ensure a fast vegetation development and prevent erosion in the first years. After sowing, a mulch layer with seed-poor green hay was applied by hand to a thickness of c. 5 cm. (ii) Hay transfer – H: The donor site for green hay was the Natura 2000 site ‘Göttersitz und Schenkenholz nördlich Bad Kösen’c. 20 km from the mined area. The vegetation consists of a mosaic of semi-natural dry grassland (Brometalia erecti Br.Bl. 1936) and mesic grassland (Dauco carotae–Arrhenatheretum elatioris (Br.Bl. 1919) Görs 1966) including 97 higher plant species. There were 71 target species (Festuco-Brometea and Arrhenatheretea spp.) (see Appendix S2 Supporting Information). On 6 September 2000, seed-rich green hay was mown with cutter bar mowers, immediately transported to the mined site Roßbach, and evenly distributed by hand at a density of c. 1 kg per m2 (5 cm thickness). (iii) Control – C: Spontaneous succession.
The area of each treatment within a block was c. 1260 m2 (18 m × 70 m, see Fig. 1) amounting to 1·13 h for the total experimental site. Three 25-m2 permanent subplots were established per treatment and block. Vegetation was surveyed annually for each subplot at the end of June from 2001 until 2009, except in 2003. The percentage cover of all species and layers was recorded. Data from the subplots within treatments and blocks were pooled for statistical analyses. Management took place in August 2002 and 2007 (mowing), and July 2005 (manual removal of woody plants).
Mean values for plant species richness (number of species per 75 m2), percentage cover of vascular plants and cryptogam species were calculated for each treatment and each year (n = 3, data collected on subplots within a block were pooled prior to analyses). For the last observation year, we tested for treatment effects on species richness and vegetation coverage using generalized linear models (GLM) followed by planned comparisons of least square means between treatments with and without species introduction (simple contrast analysis; S, H vs. C).
We used nonmetric multidimensional scaling (NMDS) to analyse the differences in vegetation composition between the three different treatments (S, H, and C). NMDS ordination was based on Bray–Curtis distances ranging from 0 (completely identical) to 1 (completely dissimilar). We estimated Bray–Curtis distances between treatments for each year. ‘Stress’ indicates the goodness-of-fit with values <0·2 corresponding to an acceptable indication of the similarities between samples (Clarke 1993). NMDS was calculated using the statistical software package PAST (PAlaeontological STatistics, ver. 2.0, Hammer, Harper & Ryan 2001). We applied repeated-measures anova to test whether species composition became increasingly similar with time. Mauchly’s test indicated that the assumption of sphericity had been violated for the main effect of ‘year’ (χ2 = 80·49, d.f. = 27, P < 0·001). Therefore, the degrees of freedom were corrected using Greenhouse-Geisser estimates of sphericity (ε = 0·55).
To analyse community composition, we used species lists from the whole study area (2·3 km2) as well as from the donor site and the sown seed mixture and divided all plant species recorded in plots at the experimental site (1·13 ha) into the following groups: (i) target species that were introduced by sowing and/or hay transfer and which were not present in the study area; (ii) target species that were introduced by sowing and/or hay transfer but that may also have colonized the experimental site through seed rain from adjacent populations within the study area; (iii) target species that were not introduced having colonized the experimental site through seed rain from adjacent populations within the study area; and (iv) nontarget species. The target species included all grassland species typically occurring in and around Arrhenatherion as well as Festuco-Brometea-communities according to the regional phytosociological literature (Schubert 2001). Calamagrostis epigejos and all other species (mostly ruderals) were considered as nontarget species. Univariate GLMs were used to test for treatment effects on the number and coverage of target and nontarget species in the last observation year.
We applied the Markov approach to analyse and compare rates and pathways of vegetation development (e.g. Usher 1992). For each treatment, we constructed a transition matrix P having elements pij that represent transition probabilities from state i to j over time. We assessed the probability of colonization by target species and nontarget species (C. epigejos and ruderals) as well as the probability that one group is replaced by another. The assessment was based on the area covered by each group as well as by bare soil (standardized to sum to 100). We converted our multivariate ecological time series into transition probability matrices according to the approach presented in Baasch, Tischew & Bruelheide (2010). For each survey plot per treatment and each transition period, we first created an interim contingency table (s × s) based on the observed values and the following predefined model assumptions.
The entries in the diagonal vii define for a certain state (Si), the area that persisted from time t to time t + 1 estimated by using the following equation:
- (eqn 1)
The i, j entries vij define the area initially covered by one state (Si), which was then replaced by another state (Sj) estimated by using the equation:
- (eqn 2)
As a result, we obtained 27 tables (three blocks × nine time periods) per treatment. By adding the corresponding elements across all 27 tables, we obtained for each treatment a final contingency table referring to the changes observed during the whole study period. Finally, we calculated the state transition probability matrix P for all three treatments by estimating the transition probabilities pij:
- (eqn 3)
The entries of P describe the processes that determine succession: colonization, disturbance, persistence and replacement. These can be quantified for a certain state or the entire system (for details, see Baasch, Tischew & Bruelheide 2010).
- Top of page
- Materials and methods
- Supporting Information
Overview – Development of Vegetation
In treatments with species introduction (S, H), plant species already covered more than 40% of the surface in the second year of observation (Fig. 2). From 2004 onwards, vegetation cover was continuously high ranging between 70 and 90%. In contrast, there was much less cover on control plots particularly in the first 5 years. Moreover, we observed a higher cover of cryptogams for treatments S and H compared to control plots in all years. In the final year of observation, we could still detect significant treatment effects on the cover of cryptogams but not on the total cover of vascular plant species (Table 1).
|Year||Dependent variable||Univariate GLM||Contrasts (simple, reference category: control)|
|F||P||P||(S vs. C)||P||(H vs. C)|
|2009||Coverage of cryptogams||11·27||0·009||0·007||(S > C)||0·006||(H > C)|
|Coverage of plant species||5·01||0·053||–||–|
|Plant species richness||1·62||0·274||–||–|
|Number of nontarget species||43·80||<0·001||<0·001||(S < C)||<0·001||(H < C)|
|Coverage of nontarget species||6·62||0·030||0·022||(S < C)||0·018||(H < C)|
|Number of target species||3·37||0·104||–||–|
|Coverage of target species||9·36||0·014||0·029||(S > C)||0·005||(H > C)|
In the first year of observation, treatments with species introduction exhibited higher species richness than control plots. However, the number of plant species decreased considerably in the following 3 years (Fig. 2). This was caused by a decrease in ruderal and annual species, but it was also owing to a rapid expansion of introduced legumes to the detriment of other target species. However, in the final observation year, we could not detect a significant treatment effect on species richness, indicating that all three treatments achieved the same level of diversity after 9 years (Table 1).
Erosion processes were controlled by the mulch layer and the fast vegetation development. Thus, we did not find erosion channels deeper than 5 cm in treatments with mulch seeding and hay transfer. Erosion was severe on control plots in the first two years where we found many erosion channels up to 1·5 m depth (particularly on the lower slope, see Fig. 3).
Except in the first 2 years, dissimilarity was slightly higher between the two different treatments with species introduction (S-H) than between these treatments and control plots (C-S, C-H; Fig. 4). Using repeated-measures GLMs, we found a significant main effect of ‘year’ on the distance between treatments (F = 95·72, P < 0·001). Contrasts revealed that the distance between treatments in the last observation year was significantly lower than the distances measured in all the previous years (except 2008), indicating that vegetation composition converged on different treatments. The between-subjects effect (comparison of treatment: S-H, C-S, C-H) was not significant (d.f. = 2, 24, F = 0·87, P = 0·430). Thus, the results suggest that the similarity in vegetation composition increased with time across all three treatments. Despite this converging trend, the overall similarity between treatments remained quite low until the final observation year (dissimilarity S-H: 0·64 ± 0·07 SD, C-S: 0·62 ± 0·06 SD, C-H: 0·62 ± 0·07 SD).
We found a high number of nontarget species in all treatments in the first 2 years (Fig. 5a). In particular, short-lived ruderal and segetal species (e.g. Bromus sterilis, Chenopodium album, Descurainia sophia, Lepidium campestre, Papaver rhoeas, Polygonum aviculare, Reseda luteola, Thlaspi arvense, Tripleurospermum maritimum) frequently reached the experimental site through seed rain. Additionally, some less-competitive ruderals were purposefully introduced by the sowing treatment to ensure faster revegetation and prevent erosion (e.g. Poa annua, P. compressa).
The number of nontarget species decreased with time for all three treatments; this decrease was more pronounced in treatments with species introduction. However, the coverage of nontarget species increased with time (Fig. 5b). Control plots showed a considerably higher increase in nontarget species’ cover, mainly caused by the clonal spread of C. epigejos between 2004 and 2009. For the final observation year, we found significant treatment effects on the number and coverage of nontarget species, which were both significantly higher in control plots than in plots with sowing or hay transfer treatments (Table 1).
Typical grassland community species developed best in the hay transfer treatment. We found between 30 and 40 target species with a cumulative vegetation cover of more than 70% from 2004 onwards (Fig. 5c,d). Transfer rates (i.e. the number of species found on treated plots as a percentage of the number of species that occurred in the donor site ‘Göttersitz’) differed between years, ranging from 55 to 69% with 64% in the final observation year (see also Appendix S2 Supporting Information). In addition to the common grassland species that already occurred in the mined site Roßbach (e.g. Arrhenaterum elatius, Galium album, Lotus corniculatus, Trifolium campestre), from the second year onwards, we found between 15 and 20 grassland species that had originated from the transfer of plant material (e.g. Bromus erectus, Centaurea scabiosa, Ononis spinosa, Salvia pratense).
Establishment rates in the sowing treatment (i.e. the number of species found on treated plots as a percentage of the number of sown species) were continuously high ranging from 81 to 100% (2009: 95%; see also Appendix S1, Supporting Information). However, the number of target species was not as stable as in the hay transfer treatment. This was caused by a rapid expansion of introduced legumes to the detriment of other target species. Between 2004 and 2007, the predominance of legumes was unexpectedly high (e.g. Securigera varia), which led to a significantly lower species richness in 2005 compared to the hay transfer treatment and the control plots (see also Fig. 2).
Over time, the number of target species also increased on the control plots (Fig. 5c). Some of these species clearly migrated into the control plots from adjacent treatment strips (e.g. B. erectus, C. scabiosa, O. spinosa, S. pratense, S. varia). Thus, we did not find any significant difference in the number of target species between treatments with and without species introduction at the end of our study period (Table 1). However, despite the high number of target species on the control plots, the percentage of target species within the total plant cover remained low during the whole study period. In 2009, total coverage of grassland species was around 30%, which was significantly lower than in treatments with hay transfer or sowing (Table 1).
Figure 6 represents a schematic outline of the mean transient dynamics between species groups over the whole study period. The probability that bare soil was colonized by any species group was much higher in treatments with hay transfer (0·43) and sowing (0·38) than in control plots with spontaneous succession (0·15). These treatments were mainly colonized by target grassland species, which persisted to a high degree. The colonization rate by ruderal species was low, and the probability that established ruderals would be replaced by target species over time was relatively high. Moreover, the rates of colonization and replacement by C. epigejos were notably low; thus, both treatments with species introduction prevented a rapid and massive invasion by this competitive clonal grass. On control plots with spontaneous succession, bare soil was colonized by target species as well as ruderal species and C. epigejos. However, both target and ruderal species were to some degree replaced by C. epigejos, which also had the highest probability of persistence.
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- Materials and methods
- Supporting Information
Restoration through direct addition of appropriate seeds via green hay and sowing clearly accelerated successional progress at our experimental sites. Moreover, both treatments not only favoured the rapid establishment of plant species but also facilitated the establishment of cryptogams (see also Poschlod & Biewer 2005; Jeschke & Kiehl 2006) and provided effective erosion control (see also Kirmer & Mahn 2001). The hay mulch in both treatments may also have facilitated seedling establishment and growth on the nutrient-deficient slope (see also Kirmer, Baasch & Tischew 2011; Tongway & Ludwig 2011) owing to improvements in soil structure, moisture capture and retention, fertility and biological activity (e.g. Bradshaw 1983; Grant, Campbell & Charnock 2002; Bakker et al. 2003; Cummings et al. 2005).
The spread of target species that were not present in the mined site prior to the experiment indicates that these species generally are able to grow under postmining conditions but were seed-limited before hay transfer or direct sowing. Limited dispersal capability has often been shown to be an obstacle for successful grassland restoration (e.g. Bakker et al. 1996; Bullock et al. 2002; Donath, Hölzel & Otte 2003; Bossuyt & Honnay 2008; Bischoff, Warthemann & Klotz 2009), and propagule pressure has been shown to be a major driver of community assembly (e.g. Von Holle & Simberloff 2005). Large-scale mined sites act as huge seed traps in the landscape (Kirmer et al. 2008), providing a large number of niches for (re)colonization of species well adapted to open habitats (e.g. Bradshaw 1983; Ash, Gemmell & Bradshaw 1994; Schulz & Wiegleb 2000; Kirmer et al. 2008) and thus can generate highly diverse habitats (e.g. Prach & Pyšek 2001; Prach 2003; Tischew & Kirmer 2007; Řehounková & Prach 2008). However, these processes take time. The transfer of green hay and sowing of site-specific seed mixtures of local provenance can accelerate this process considerably leading to the rapid establishment of species-rich grasslands. Thus, our results are in line with several studies from other restoration sites (e.g. ex-arable fields), showing that the use of near-natural restoration methods leads to high establishment rates of target grassland species (e.g. Pywell et al. 2002; Hölzel & Otte 2003; Kiehl, Thormann & Pfadenhauer 2006; Jongepierová, Mitchley & Tzanopoulos 2007; Lepšet al. 2007; Török et al. 2010; for review see Kiehl et al. 2010).
Moreover, application of green hay as well as direct sowing not only affected the speed of succession, but also the pathway. In spontaneously developing sites, C. epigejos migrated from nearby source populations, expanded by vegetative means, showed a high persistence rate and thus became increasingly dominant over time. In Central European man-made habitats, Calamagrostis is very common, often forming dense swards and can even arrest succession altogether for a long time period (e.g. Prach & Pyšek 2001; Rebele & Lehmann 2001; Wiegleb & Felinks 2001a; Prach 2003; Tischew & Kirmer 2007; Mudrák, Frouz & Velichová 2010). Therefore, if potentially ‘problematic’ species (e.g. ruderal or invasive species) occur in the proximity of restoration sites, spontaneous succession might not successfully recreate species-rich grasslands (see also Prach & Hobbs 2008). These results confirm our first hypothesis.
Species introduction via hay transfer and sowing had a long-term effect on species composition and the number of target species. Once established, the species-rich grasslands were highly resistant to invasion by Calamagrostis and other ruderals even though management was rather sporadic. Stable grassland communities developed best in the hay transfer treatment, while in the sowing treatment, the high productivity of legumes caused a temporary decrease in species diversity in 2005 and 2006. However, as in other experiments, the predominance of legumes did not persist over the long term (e.g. Pfisterer et al. 2004; Petermann et al. 2010). Compared to the artificial seed mixture, the seed composition of the harvested green hay may have been more balanced (species number and species identity), resulting in stable and continuous vegetation development towards the intended target community. Moreover, the number of potentially transferable species in hay was five times higher than the number of sown species. Other studies (e.g. Pakeman, Pywell & Wells 2002; Pywell et al. 2002; Walker et al. 2004; Lepšet al. 2007) have also found that highly diverse seed mixtures are more successful in creating species-rich grasslands and that species turnover is low compared to less diverse seed mixtures.
As has been found in other grassland re-creation experiments (e.g. Pakeman, Pywell & Wells 2002), species introduced elsewhere in the experiment migrated into the other treatments. In our experimental site, the number of target species continues to increase on the control plots owing to both migration of target species that were already present in the mining area and migration of target species that have been introduced in adjacent treatments. Thus, successful propagation of local species and species exchange led to a converging trend in species composition between treatments. Interestingly, 9 years after the start of the experiment, we did not find any significant differences between treatments with and without species introduction in terms of total vegetation cover, species richness and the number (but not cover) of target species. However, our experimental site offered ideal conditions with nearby seed sources from adjacent treatments and thus our results are not representative of field-scale restoration projects. In extensively disturbed areas, appropriate seed sources are often long distances away. If connectivity is low, the possibility of target species colonizing the sites may decrease drastically (e.g. Walker et al. 2004). Successful colonization via long-distance dispersal through natural processes takes longer than a few years (Ash, Gemmell & Bradshaw 1994; Brändle et al. 2003; Kirmer et al. 2008). Finally, despite the possibility of species exchange, the overall similarity in community composition between treatments remained quite low until the final observation year. The dominance ratio between target and nontarget species still differed significantly, as treatments where species were introduced still showed a higher abundance of target species and a lower coverage of ruderals. Hence, our results confirm our second hypothesis highlighting the importance of initial floristic composition and the order of species arrivals (e.g. priority effects of competitive species) in vegetation development and convergence to the same species composition.
The application of green hay and direct sowing regional seed mixtures considerably affected both the speed and the pathway of vegetation succession in the restoration sites. Both methods are appropriate restoration tools when rapid vegetation development is desired for aesthetic reasons or erosion control, when no potential seed sources of target species are available nearby, when species with low dispersal capacity are preferred and finally when there is a need to suppress unwanted species. An additional mulch layer is recommended on sites susceptible to erosion. Our results demonstrate that introduced grassland species are able to colonize adjacent nutrient-poor but hospitable sites. Therefore, in large-scale restoration areas with suitable site conditions, we recommend the application of seed-rich green hay or sowing of regional seed mixtures in strips to allow for natural colonization in the intervening gaps resulting in mosaic biotopes of different grassland types.
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- Materials and methods
- Supporting Information
The study was funded by the German Foundation for the Environment (DBU), the European Union (Interreg IIIB CADSES, Interreg IVB Central Europe), the German Federal Ministry for Education, Science, Research and Technology (BMBF) and the Lausitz and Central-German Mining Administration Company (LMBV). We are grateful to all people who helped to collect the data and to Keith Edwards who kindly checked the English. Finally, we thank the editor and two anonymous reviewers for providing constructive comments.
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- Supporting Information
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- Top of page
- Materials and methods
- Supporting Information
Appendix S1. Seed mixture used for slope restoration (sowing treatment) in the mined site Roßbach.
Appendix S2. List of 97 higher plant species from the donor site ‘Göttersitz’ used for hay transfer.
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