The availability of seeds and microsites are limiting factors for many plant species of different vegetation types. We have investigated the existence of such limitations in two habitats, an alpine heath and a subalpine birch forest, where abiotic factors are hypothesized to be the main determining factor of plant species distributions. Both habitats are characterized by a short growing season and cold temperatures, and the alpine heath is also constrained by low productivity. A seed addition experiment including six vascular plants, selected by different functional traits and occurrence, showed that seed limitation was an important factor in these habitats. Removal of the aboveground biomass (controlled disturbance) increased germination only for some species. The effect of reindeer presence was found to be of less importance, probably due to low and varying densities of reindeer. To conclude, we found that seed limitation was the most important factor limiting the distribution of our studied species in the two alpine environments.
Germination, and thereby population dynamics, for many species of different types of vegetation is limited by the availability of seeds (Turnbull et al., 2000) and by suitable microsites for seeds to germinate in. Seed limitation and microsite limitation may act in combination if germination is favored not only by seed addition but also by small-scale disturbances (e.g. Eriksson and Ehrlén, 1992; Jakobsson and Eriksson, 2000; Eskelinen and Virtanen, 2005). We found it especially important to study limitations for germination in plant species in alpine and subalpine environments where plant distributions often are assumed to be structured by abiotic factors (Körner, 2003). Sexual reproduction is stochastic, and alpine plants experience large variation among years in both seed production and seedling establishment (Chambers, 1995; Larsson and Molau, 2001). Even though sexual reproduction is rare and many plants rely on vegetative propagation and have a capacity for being long-lived (Jonsdottir et al., 2000), occasional seedling recruitment is important for maintaining genetic diversity of populations and for colonization of previously unoccupied sites (Eriksson, 1993). In closed vegetation microsite availability might be enhanced by mammals, e.g. trampling by reindeer (Rangifer tarandus) and digging by rodents (Moen et al., 1993). Such disturbances may have positive effects on some plant species, by creating gaps for recruitment in a dense vegetation cover, or have negative effects when the disturbance is extensive, resulting in bare soil patches (Austrheim and Eriksson, 2001; Klug et al., 2002; Cairns and Moen, 2004; Olofsson et al., 2004, 2005). Biotic interactions among plants might influence seedling germination both positively by facilitation and negatively by competition (Dormann and Brooker, 2002; Olofsson, 2004). Facilitation among species exists if the establishment and growth of a species is enhanced by the presence of other species, and some studies indicate that the importance of facilitation increases in harsh environments (Wipf et al., 2006). However, other studies have shown that competition could be an important factor limiting the establishment of plant species in alpine environments, and the relative importance of facilitation and competition will vary across gradients of abiotic stress (Maestre et al., 2005).
The alpine heath is dominated by a vegetation cover consisting of a dense layer of ericaceous shrubs with low productivity, while the vegetation cover in the subalpine birch forest is dominated by birch, herbs, grasses, mosses, and liverworts, with relatively high nutrient availability. We studied the importance of seed availability and microsite availability for the germination of six selected vascular plant species in these two habitats. Although the presence and density of reindeer is variable between years and grazing and trampling effects are extensive in the study area, we expect reindeer presence to enhance germination by the creation of small gaps and by reducing the accumulation of litter (Virtanen, 2000). In addition, we recorded seedlings of other species, present in the vicinity of the study area but not included in the seed addition experiment, in order to assess the importance of reindeer presence and disturbance for natural seedling recruitment.
Study Species and Sites
Six species were used in the sowing experiment (Table 1). Henceforth they are referred to by their generic names. The species were selected based on their functional traits such as life span, seed size, dispersal mode, and occurrence in order to get a subset of species with a wide spectrum of different traits. None of the species is known to have an extensive persistent seed bank.
The species used in the sowing experiments, their life forms, seed weights, dispersal attributes, and the most characteristic habitat. Data collected from field sampling or literature (Grime et al., 1988; Peat and Fitter, 2005).
The study sites were situated in the vicinity of Ammarnäs, southern Lapland, Sweden (66°N, 16°E). Two sites were located above the tree line on the alpine heath, at an altitude of 800–1100 m a.s.l., and two sites were located in the subalpine birch forest, at an altitude of 500–650 m a.s.l. The heath sites were dominated by mosses, lichens, dwarf shrubs, grasses, and sedges. The birch forest sites were situated in humid slopes where tall herbs dominated the shrub layer. Mosses, liverworts, Vaccinum myrtillus, graminoids, and small herbs were significant constituents of the herb layer. All four sites were inhabited by free ranging reindeer (Rangifer tarandus) during the summer season, with densities varying between years.
Forage selection by reindeer at landscape level is mainly determined by forage biomass, predation, and insect harassment (Rettie and Messier, 2000; Mårell et al., 2002; Skarin et al., 2004). Once in the vicinity of the experimental plots, reindeer could be attracted to the plots by curiosity or avoid the plots because of a lack of biomass, but forage patch selection is mainly shown to be structured by forage quality, and the experimental plots are too small to alter the food quality of the sites.
At each site, a large reindeer exclosure (100 m × 100 m) was built in 1996. Close to each exclosure, an equivalent control area where reindeer had access was chosen. In each of the exclosures and in the control areas, 40 plots of the size of 20 cm × 20 cm were placed (10 per treatment). The experiment with artificial disturbance and seed addition consisted of four different treatments: seeds added/not added combined with plots disturbed/not disturbed. In total, about 32,000 seeds from each of the experimental species were collected in the study area (seeds of Rhinanthus were collected in the vicinity of the village of Ammarnäs). The seed addition treatment consisted of sowing a seed mix in 1999 of 200 seeds of each of the six investigated species per 4 dm2 plot, based on the findings of Lindborg (2006), where it was shown that 50 seeds dm−2 per species was an optimal seed density. Since the germination rate was relatively low and since the germination of naturally occurring seeds was independent of the seed addition experiment (see Results), direct interactions between seeds and/or seedlings can be regarded as negligible. Seeds from fleshy fruits were extracted before sown. All seeds were distributed immediately after collection. The disturbance treatment consisted of the removal of all aboveground vegetation before seed addition in 1999 and was not repeated the following years since it risked removing seeds/seedlings and since there were not much inward growth from the perimeters.
The experiment was initiated in August 1999 and the seedlings emerging in the plots were recorded at the end of July for three years (2000–2002). Since it was not possible to follow seedlings individually, the response variable analyzed, “germination,” was the total number of emerging seedlings within the three years. Double counting could be avoided because aged seedlings can be distinguished from recent ones. In addition to the experimental species, seedling emergence of other species was also recorded in order to assess the importance of grazing and disturbance for natural seedling recruitment. It should be noted that we have no information on the seed availability of the species recruiting naturally in the plots.
Due to low recruitment, and thus many zeros in the database for plots without seed addition, the intended use of a split-plot ANOVA was not feasible. Therefore, we divided the analyses into two steps, where we first tested if the presence of reindeer affected seed germination with a Mann-Whitney U-test. In this test, we used the pooled data from both habitats, both sites in each habitat, and for both seed addition and disturbance treatments. In the cases where reindeer presence had no effect, we analyzed the effect of the treatments on the pooled data from both the control (reindeer present) and the exclosures (reindeer absent) with a Generalized Linear Model with a Poisson distribution. In the cases where reindeer presence had a significant effect (Trollius), we analyzed the effect of the treatments separately with data from the exclosures and outside the exclosures, respectively (see Table 2). The number of seedlings was square-root-transformed before analysis, but the figures are based on back-transformed data. Data on seedlings of other species were analyzed in the same way as Trollius, since reindeer presence had an effect on the germination of other species. Data on seedlings of other species is collected only from the birch forest since there were very few seedlings of other species germinating in the alpine heath.
The effects of reindeer presence on the germination of the six species included in a seed addition experiment (N = 160) and other seedlings, and Ranunculus acris (N = 80), tested with Mann-Whitney U-tests. Significant results are in bold.
Our results indicate that the presence of reindeer do not have a strong effect on the germination of seedlings of the experimental species, except for Trollius europeus, where germination was more successful inside the reindeer exclosures (Table 2 and Fig. 1) Five species (all except Empetrum) germinated in the birch forest and all of those were favored by seed addition (Table 3). Only three species germinated in the alpine heath, two of which, Rumex and Vaccinium, were favored by seed addition (Table 3). Removal of aboveground biomass increased germination for Rumex and Vaccinium (Table 3, Figs. 1 and 2). There were differences in germination between the two habitat types, since Trollius, Rhinanthus, and Cicerbita seedlings only emerged in the birch forest. Empetrum germinated only in the alpine heath, but in very low numbers. Rumex and Vaccinium germinated in both habitats, with Rumex more strongly in the alpine heath than in the birch forest.Figure 3Table 4
The effects of habitat, seed addition, and disturbance on the study species where reindeer presence was not of significant importance for germination, analyzed with a Generalized Linear Model (GLZ) with Poisson distribution. Significant results are in bold.
The effects of habitat, seed addition, and disturbance on germination of Trollius and the effects of seed addition and disturbance on germination of other species, and Ranunculus acris, with and without reindeer presence, analyzed with a Generalized Linear Model (GLZ) with a Poisson distribution. Significant results are in bold.
Germination of other species in the birch forest was negatively influenced by reindeer presence (Table 2 and Fig. 1). One of the most common species among those other species, Ranunculus acris, was also negatively influenced by reindeer presence. The seed addition experiment did not affect germination of these naturally occurring seedlings, but the removal of biomass increased the germination of other species both inside and outside the reindeer exclosure. Ranunculus acris benefited from disturbance inside the exclosure, but was unaffected outside the exclosure, where reindeer had access.
Reindeer presence did not have any significant positive effects on seedling emergence, as has been shown in other studies (Fig. 3) ( i.e. Eskelinen and Virtanen, 2005). The densities of reindeer in the study area are highly variable and we could not observe any obvious trampling effects in the immediate vicinity of the experimental plots during the study period, but we could observe selective grazing on large herbs in the birch forest. Compared to the artificial disturbance, the disturbance effects by reindeer (trampling) were probably much smaller. The grazing effects by reindeer could be severe for the preferred species, but the density of reindeer was probably too low to generate effects such as a decrease of litter and aboveground biomass. The number of seedlings of other species and Trollius were negatively influenced by reindeer presence (Table 4), which could be due to selective grazing, as we did see that reindeer often preferred reproductive parts of the plants (Mårell et al., 2002), and thus could decrease the amount of seeds locally (Cooper and Wookey, 2003).
In contrast to disturbances by reindeer, the controlled disturbance, where the aboveground biomass was removed, had significant positive effects on some species, indicating that competition from other plant species limit the availability of suitable microsites for those species. Gough (2006) also found that seed germination rates were significantly higher in an arctic plant community where mosses and vascular plants were removed compared to plots with intact vegetation. Three of the species only occurring in the birch forest, Rhinanthus, Trollius, and Cicerbita, were not affected by disturbance, and similar results were found for Rhinanthus also in a study by Austrheim and Eriksson (2003). Seed weight and recruitment have been found to be positively correlated (Westoby et al., 1997; Turnbull et al., 1999) and large-seeded, non-clonal species are successful in the phase of seedling emergence even in closed vegetation, as large seeds allow them to emerge, effectively disregarding competition from other species (Welling and Laine, 2002). However, the light seeds from Cicerbita and the intermediate-sized seeds from Trollius (see Table 1) also showed the same pattern, which is harder to explain by the seed weight. Rhinanthus is hemiparasitic, and the availability of suitable host plants could affect the survival, but probably not the germination, of Rhinanthus seedlings. The low importance of small-scale disturbance could be due to the structure of the vegetation in the birch forest. The vegetation cover is very dense in the shrub layer, while the ground is only patchily covered by small herbs, grasses, and mosses, which may make the small-scale disturbance of the ground layer in this study of less importance in the birch forest.
Another structuring force in plant communities might be seed limitation (Tilman, 1997), and one definition of seed limitation is an increase in population size following seed addition (Turnbull et al., 2000). However in this study, we did not follow the demography of the species, so our definition of seed limitation is an increase in seedling density after seed addition (see also Austrheim and Eriksson, 2003). With this definition in mind, all species were seed limited to some extent except for Empetrum, were no seeds germinated in the birch forest and very few on the alpine heath. A close relative to Empetrum hermaphroditum, E. nigrum, has been shown to be a bad colonizer by Olofsson et al. (2005). In their study, E nigrum failed to colonize gaps even though it dominated the undisturbed vegetation. Another study of the genetics of different clones indicates that E. hermaphroditum establishes by seeds to a relatively large extent over a long time span (Szmidt et al., 2002). Empetrum has also been shown to produce biologically active phenolic compounds that can limit the establishment of other species (Shevtsova et al., 2005). Trollius, Cicerbita, and Rhinanthus were seed limited in the birch forest, and Vaccinium and Rumex were seed limited in both habitats. Seed limitation is also confirmed among alpine and arctic plants by recent studies of snow bed communities (Eskelinen and Virtanen, 2005) and arctic tundra plant communities (Gough, 2006). None of the species included in this study has any verified extensive seed bank longevity. Some studies of other species indicate that extensive seed banks may exist in alpine environments (e.g. Ingersoll and Wilson, 1993; Diemer and Prock, 1993; Cavieres, 1999; Welling and Laine, 2002), but there are few studies on seed bank longevity from the Scandes. There were almost no seedlings emerging from the experimental species in the plots without seeds added, indicating a seed limitation of those species. However, there were a relatively high number of seedlings of other species in the birch forest, which indicates a high occurrence of other seeds in the soil in the birch forest, especially from Ranunculus acris. The species not recruiting in the alpine heath are probably constrained by other factors than seed limitation and microsite availability, i.e. abiotic factors.
In conclusion, the subalpine birch forest and the alpine heath are differing in the germination rate of most species. Seed limitation is by far the most important factor in both habitats, while disturbance plays a more crucial role in the alpine heath. Reindeer presence does not significantly influence five of the six study species, but for Trollius and naturally germinating species in the plots, reindeer presence was negative for seed germination, probably due to selective feeding on reproductive parts of the plants.
We thank the Swedish Foundation for Strategic Environmental Research (MISTRA) for funding this project through the Mountain Mistra Programme. We also thank Regina Lindborg for valuable comments on the manuscript and Didrik Vanhoenacker for statistical advice.
- G. Austrheim and O. Eriksson . 2001. Plant species diversity and grazing in the Scandinavian mountains—Patterns and processes at different spatial scales. Ecography 24:683–695. Google Scholar
- G. Austrheim and O. Eriksson . 2003. Recruitment and life-history traits of sparse plant species in subalpine grasslands. Canadian Journal of Botany 81:171–182. Google Scholar
- D. M. Cairns and J. Moen . 2004. Herbivory influences tree lines. Journal of Ecology 93:1019–1024. Google Scholar
- L. A. Cavieres 1999. Persistent seed banks: delayed seed germination models and their application to alpine environments. Revista Chilena de Historia Natural 72:457–466. Google Scholar
- J. C. Chambers 1995. Disturbance, life-history strategies, and seed fates in alpine herbfield communities. American Journal of Botany 82:421–433. Google Scholar
- E. J. Cooper and P. A. Wookey . 2003. Floral herbivory of Dryas octopetala by Svalbard reindeer. Arctic, Antarctic, and Alpine Research 35:369–376. Google Scholar
- M. Diemer and S. Prock . 1993. Estimates of alpine seed bank size in two Central-European and one Scandinavian sub-arctic plant communities. Arctic and Alpine Research 25:194–200. Google Scholar
- C. F. Dormann and R. W. Brooker . 2002. Facilitation and competition in the high Arctic: the importance of the experimental approach. Acta Oecologia–International Journal of Ecology 23:297–301. Google Scholar
- O. Eriksson 1993. Dynamics of genets in clonal plants. Trends in Ecology and Evolution 8:313–316. Google Scholar
- O. Eriksson and J. Ehrlén . 1992. Seed and microsite limitation of recruitment in plant populations. Oecologia 91:360–364. Google Scholar
- A. Eskelinen and R. Virtanen . 2005. Local and regional processes in low-productive mountain plant communities: the roles of seed and microsite limitation in relation to grazing. Oikos 110:360–368. Google Scholar
- L. Gough 2006. Neighbour effects on germination, survival, and growth in two arctic tundra plant communities. Ecography 29:44–56. Google Scholar
- J. P. Grime, J. G. Hodgson, and R. Hunt . 1988. Comparative Plant Ecology London Unwin Hyman. Google Scholar
- C. A. Ingersoll and M. V. Wilson . 1993. Buried propagule bank of a high sub-alpine site—Microsite variation and comparisons with aboveground vegetation. Canadian Journal of Botany 71:712–717. Google Scholar
- A. Jakobsson and O. Eriksson . 2000. A comparative study of seed number, seed size, seedling size and recruitment in grassland plants. Oikos 88:494–502. Google Scholar
- I. S. Jonsdottir, M. Augner, T. Fagerström, H. Persson, and A. Stenström . 2000. Genet age in marginal populations of two clonal Carex species in the Siberian Arctic. Ecography 23:402–412. Google Scholar
- B. Klug, G. Scharfetter-Lehrl, and E. Scharfetter . 2002. Effects of trampling on vegetation above the timberline in the Eastern Alps, Austria. Arctic, Antarctic, and Alpine Research 34:377–388. Google Scholar
- C. Körner 2003. Alpine Plant Life. 2nd edition Heidelberg Springer Verlag. Google Scholar
- E. L. Larsson and U. Molau . 2001. Snowbeds trapping seed rain—A comparison of methods. Nordic Journal of Botany 21:385–392. Google Scholar
- R. Lindborg 2006. Recreating grasslands in Swedish rural landscapes—Effects of seed sowing and management history. Biodiversity and Conservation 15:957–969. Google Scholar
- F. T. Maestre, F. Valladares, and J. F. Reynolds . 2005. Is the change of plant-plant interactions with abiotic stress predictable? A meta-analysis of field results in arid environments. Journal of Ecology 93:748–757. Google Scholar
- A. Mårell, J. P. Ball, and A. Hofgaard . 2002. Foraging and movement paths of female reindeer: insights from fractal analysis, correlated random walks, and Levy flights. Canadian Journal of Zoology 80:854–865. Google Scholar
- J. Moen, H. Gardfjell, L. Oksanen, L. Ericson, and P. Ekerholm . 1993. Grazing by food-limited microtine rodents on a productive experimental plant community—Does the green desert exist?. Oikos 68:401–413. Google Scholar
- J. Olofsson 2004. Positive and negative plant-plant interactions in two contrasting arctic-alpine communities. Arctic Antarctic, and Alpine Research 36:464–467. Google Scholar
- J. Olofsson, P. E. Hulme, L. Oksanen, and O. Suominen . 2004. Importance of large and small mammalian herbivores for the plant community structure in the forest tundra ecotone. Oikos 106:324–334. Google Scholar
- J. Olofsson, P. E. Hulme, L. Oksanen, and O. Suominen . 2005. Effects of mammalian herbivores on revegetation of disturbed areas in the forest-tundra ecotone in northern Fennoscandia. Landscape Ecology 20:351–359. Google Scholar
- H. Peat and A. Fitter . 2005. The ecological flora of the British Isles at the University of York ( http://www.york.ac.uk/res/ecoflora/cfm/ecofl/Detail_ecochars.cfm?PLANT_NO = 610060010). Cited 14 December 2005. Google Scholar
- W. J. Rettie and F. Messier . 2000. Hierarchical habitat selection by woodland caribou: its relationship to limiting factors. Ecography 23:466–478. Google Scholar
- A. Shevtsova, M. C. Nilsson, C. Gallet, O. Zackrisson, and A. Jaderlund . 2005. Effects of long-term alleviation of nutrient limitation on shoot growth and foliar phenolics of Empetrum hermaphroditum. Oikos 111:445–458. Google Scholar
- A. Skarin, Ö Danell, R. Bergström, and J. Moen . 2004. Insect avoidance may override human disturbances in reindeer habitat selection. Rangifer 24:95–103. Google Scholar
- A. E. Szmidt, M. C. Nilsson, E. Briceno, O. Zackrisson, and X. R. Wang . 2002. Establishment and genetic structure of Empetrum hermaphroditum populations in northern Sweden. Journal of Vegetation Science 13:627–634. Google Scholar
- D. Tilman 1997. Community invisibility, recruitment limitation and grassland biodiversity. Ecology 78:81–92. Google Scholar
- L. A. Turnbull, M. Rees, and M. J. Crawley . 1999. Seed mass and the competition/colonization trade-off: a sowing experiment. Journal of Ecology 87:899–912. Google Scholar
- L. A. Turnbull, M. J. Crawley, and M. Rees . 2000. Are plant populations seed-limited? A review of seed sowing experiments. Oikos 88:225–238. Google Scholar
- R. Virtanen 2000. Effects of grazing on above-ground biomass on a mountain snowbed, NW Finland. Oikos 90:295–300. Google Scholar
- P. Welling and K. Laine . 2002. Regeneration by seeds in alpine meadow and heath vegetation in sub-arctic Finland. Journal of Vegetation Science 13:217–226. Google Scholar
- M. Westoby, M. Leishman, and J. Lord . 1997. Comparative ecology of seed size and dispersal. In J. Silvertown, M. Franco, and J. Harper , editors. eds. Plant Life Histories: Ecology, Phylogeny and Evolution Cambridge Cambridge University Press. Google Scholar
- S. Wipf, C. Rixen, and C. P. H. Mulder . 2006. Advanced snowmelt causes shift towards positive neighbour interactions in a subarctic tundra community. Global Change Biology 12:1496–1506. Google Scholar