Reindeer Winter Grazing in Alpine Tundra: Impacts on Ridge Community Composition in Norway

ABSTRACT

We analyzed lichen species composition and biomass in 815 plots on 163 sites across wild reindeer regions in Norway, ranging from ranges with a long history of very low grazing pressure to heavily grazed sites. Reindeer density (1974–2000) and lichen biomass were well correlated for sites with comparable snow cover, altitude and terrain (R ²  =  0.81, P  =  0.006, n  =  12). Absence of grazing for potentially several centuries has virtually resulted in a monoculture consisting of Cladina stellaris, Flavocetraria nivalis, and Alectoria ochroleuca (Syn. Bryocaulon ochroleuca). Light grazing in terms of 20 to 30% removal of initial lichen cover easily eroded Cladina stellaris from exposed ridges by cratering and trampling by reindeer through the snow, while Flavocetraria nivalis persisted longer. This decline in lichen cover observed along a historic grazing gradient further resulted in increasing cover of bare ground, but less than expected from lichen removal due to gradual colonization of other species, such as mosses (incl. Polytrichum piliferum), crustose and fruticose lichens, dwarf shrubs (Arctostaphylos spp., Empetrum nigrum, Loiseleuria procumbens), and graminoids, particularly rushes (Juncus trifidus). Moderate grazing may thus increase plant diversity on ridges compared to ungrazed lands, and hence strongly influence gradients in biomass, composition and abundance of ridge communities across the landscape.

Introduction

Herbivores are well known to influence plant succession patterns, nutrient cycling, and vegetation community structures (Oksanen and Oksanen, 1989; Olofsson et al., 2002, 2004a, 2004b, 2005; Virtanen et al., 2006). There are numerous studies on the role of ungulate grazing for vegetation composition (i.e., Manseau et al., 1996; Augustine and McNaughton, 1998; Bråthen and Oksanen, 2001; van der Wal, 2006). In arctic and alpine environments, where diversity of ungulates is much lower than in tropical ecosystems, permafrost, geomorphology and the short growing season provide highly different conditions for plant growth and colonization of disturbed or heavily grazed areas than in more temperate and tropical regions (Forbes and Jefferies, 1999; van der Wal et al., 2001a, 2001b).

Ground lichens comprise a primary food source for reindeer and caribou (Rangifer tarandus) in alpine regions, along with grasses, sedges, herbs, and dwarf shrubs (Bergerud, 1974; Gaare and Skogland, 1975; Helle, 1984; Danell et al., 1994; Parker et al., 2005). Due to their slow growth, lichens can easily be depleted by intensive grazing at high Rangifer densities (Skogland, 1985; Ouellet et al., 1993; Jefferies et al., 1994; Boudreau and Payette, 2004a; Mysterud, 2006). Depletion of lichens following an increase in reindeer or caribou populations has been recorded throughout the circumpolar North, such as in Norway (Tveitnes, 1980; Skogland, 1988; Gaare, 1995; Johansen and Karlsen, 2005), West-Greenland (Staaland and Olesen, 1992), eastern Canada (Couturier et al., 1990; Manseau et al., 1996), Russia (Ahti and Oksanen, 1990; Vilchek, 1997; Crittenden, 2000), and in particular in the extreme situations of introduced caribou herds to islands without a previous history of grazing (Klein, 1968, 1987; Heard and Ouellet, 1994).

A depletion of the lichen cover has often been observed in conjunction with increased vulnerability to icing conditions, reduced body weights of Rangifer, as well as increased mortality rates and low calf production (Messier et al., 1988; Johansen and Karlsen, 2005). Although reindeer and caribou can adjust to lichen-free diets (Leader-Williams, 1988; Mathiesen et al., 1999), lichens are a vital carbohydrate source for most Rangifer in winter.

The abundance of sites available for grazing in winter, and thus the availability of lichens and food plants, depends mainly on snow conditions (Pruitt, 1959; Skogland, 1978; Helle, 1984; Adamczewski et al., 1988) and terrain ruggedness (Nellemann, 1996). Reindeer will dig craters on exposed ridges with shallow snow cover to access the lichens. In this cratering process, some lichens are kicked loose in the snow, while others are more resistant to trampling and are grazed at the bottom of the craters. The composition of lichens will therefore provide an indication of both grazing pressure and of the sensitivity of lichens to cratering (Nellemann et al., 2000). This is especially true in tundra and coastal regions, where strong winds and freeze-thaw processes pack the snow and form ice layers, but is also important in inland and alpine areas. Lichens may in particular constitute a large proportion of the diet in late winter, when windblown ridges support the only readily available forage (Bergerud, 1974; Gaare and Skogland, 1975; Mathiesen et al., 2000).

The decisions of where to eat, when to eat and what to eat are complex functions of factors such as the nutritional demands of the animal, the availability and quality of forage, cost of foraging, predator avoidance, terrain preferences, and environmental changes (Schluter, 1981; Mangel and Clark, 1986; Johnson et al., 2001). Reindeer and caribou can adapt to a variety of environmental conditions and landscapes using different foraging strategies (Johnson et al., 2001), and are often classified as intermediate mixed feeders based on characteristics of their digestive system (Mathiesen, 1999; Hofmann, 2000; Clauss et al., 2006; but see also Klein, 1985 and Staaland and White, 1991). Johnson et al. (2001) found that woodland caribou selected sites with shallow snow and a relatively high abundance of specific lichen species. Choices varied somewhat according to the scale studied; at the finest scale measured, reindeer chose between different lichen species present.

Rangifer lichen preferences have also been studied under more controlled conditions through numerous rumen content and fecal analyses, as well as in cafeteria trials (Gaare and Skogland, 1975; Holleman and Luick, 1977; Danell et al., 1994; Mathiesen et al., 2000). Several studies have assessed impacts of reindeer grazing on ground cover vegetation using remote sensing (Väre et al., 1996; Colpaert et al., 2003; Johansen and Karlsen, 2005), comparing vegetation in enclosures with grazed areas (Leader-Williams et al., 1987; Väre et al., 1995; den Herder et al., 2003) or by general vegetation surveys (Tømmervik et al., 2004), focusing on the increase of plant communities such as shrubs and grasses, as well as bare soil. Several studies have addressed vegetation changes in boreal forests and low-alpine zones (Austrheim and Eriksson, 2001; den Herder et al., 2003; Boudreau and Payette, 2004b; Eskelinen and Oksanen, 2006), but few studies have assessed vegetation transitions with different grazing pressure on arctic and alpine ridges from historic ungrazed to heavily grazed locations (Henry and Gunn, 1991; van der Wal et al., 2001a, 2001b). Such ridges are of particular interest in range ecology, being the only sites available to arctic ungulates in late winter; as well as representing severe growth conditions in relation to drainage and exposure. Several studies have documented changes in vegetation composition in boreal forests or in tundra following disturbance or grazing (i.e., Forbes and Sumina, 1999; Olofsson et al., 2005), showing changes in lichen composition as well as in colonization rates of bryophytes and graminoids (Väre et al., 1995; Virtanen et al., 1997).

Around 1900, wild reindeer were near absent in Norway due to hunting, except for the herd in Snøhetta and northern Rondane. Reindeer in southern Rondane were first reintroduced in 1972 (Jordhøy and Skogland, 1985). This means that some of the ranges investigated here have had little or no grazing for around a century (Dahl, 1956). Other ranges have been exposed to successive periods of heavy grazing and depletion of the lichen layer since the 1960s (Gaare, 1968; Skogland, 1986), hence enabling us to address the entire grazing gradient as it has evolved through the century. Herein, we analyze the composition and colonization of vegetation on ridges with comparable altitude and snow conditions along a grazing gradient.

Methods

Study Area

In south-central Norway, the original wild reindeer regions have been fragmented into some 23 smaller, largely disconnected regions holding separate populations with modest or no interaction. The fragmentation has also resulted in a disproportionate distribution in the availability of summer and winter ranges among the herds (Skogland, 1983). Wild reindeer numbers are monitored by aerial and ground surveys, and regulated through organized hunting in fall. Predation pressure is very low in the study area, predators being limited to a few wolverines (Gulo gulo) and golden eagles (Aquila chrysaetos; Ministry of the Environment, 2003; Sæther et al., 2003).

The study was conducted in four wild reindeer regions; Rondane (58 sites, 290 plots), Snøhetta (59 sites, 295 plots), Nord-Ottadalen (21 sites, 105 plots) and Nordfjella (25 sites, 125 plots; Fig. 1, Table 1). There were differences in reindeer densities both within the ranges as well as across them, partly resulting from varying degrees of human activity within the ranges, where areas within 2 to 5 km of resorts and major traffic corridors are used much less by wild reindeer compared to areas away from human activity (Nellemann et al., 2000; 2001; Vistnes et al., 2001; 2004). The ranges have also historically been exposed to different grazing pressures as mentioned above. Annual precipitation ranged from 500 to 2500 mm, being highest in the west. We studied reindeer winter grazing grounds between 1000 and 1500 m a.s.l. (in data analyses further restricted to 1100–1400 m a.s.l.) on windblown ridges above the treeline. Vegetation on ridges was dominated by lichen species, but included also occasional grasses, sedges (Carex spp., Kobresia myosuroides, Luzula spp.), rushes (Juncus trifidus), mosses (Racomitrium lanuginosum and Polytrichum piliferum), and dwarf shrubs (Arctostaphylos spp., Loiseleuria procumbens, Betula nana and Empetrum nigrum). Lichens included Cladina stellaris, Flavocetraria nivalis, Alectoria ochroleuca (Syn. Bryocaulon ochroleuca), and to a lesser extent Alectoria nigricans, Bryocaulon divergens, Flavocetraria cucullata, and Thamnolia vermicularis. Lichens on rocks included Hypogymnia (syn. Parmelia) alpicola, Rhizocarpon geographicum, and Umbilicaria spp. Cladina rangiferina, Cladina mitis, Cladonia spp., Stereocaulon spp., and Cetraria spp. were common farther down the ridge, but were in general not included in this study as we focused on exposed ridges which depict grazing patterns most clearly (Nellemann et al., 2000).

Figure 1 Location of the study areas Rondane, Nord-Ottadalen, Snøhetta, and Nordfjella wild reindeer regions in Southern Norway.

Table 1 Distribution and time of field work (vegetation and snow registration) for 163 sites in wild reindeer winter grazing habitat.

Lichen and Snow Measurements

A total of 163 sites, each 20 × 50 m, were randomly placed within the four study areas using a 100 × 100-m grid and a random digit table. A 100 × 100-m grid was placed across a 1:50,000 map and x-y coordinates for individual sites were selected using a random digit table, where the ridge nearest the random point was used for the site. A 10 × 10-m grid covering this ridge was used to place the site along the ridge on a similar basis. Sites were restricted to exposed ridges with no or little snow in lichen heaths between 1000 and 1500 m a.s.l. (Table 1). In cases when field work was conducted in summer, sites were first marked the previous winter to relocate exposed ridges available in winter. At each site, we measured cover of major lichen species within five 1 × 1-m random plots, using a 1 × 1-m grid system covering the 20 × 50 m site, and, again, the random digit table. If in winter, snow was cautiously removed from the site using a small shovel and a soft brush, ensuring that as few vegetation fragments as possible were removed. Vegetation cover of dominant or common lichen species (Cladina stellaris, Flavocetraria nivalis, Flavocetraria cucullata, Alectoria ochroleuca, Alectoria nigricans, Bryocaulon divergens, Thamnolia vermicularis, Umbilicaria spp., and Hypogymnia alpicola were recorded by counting the number of 10 × 10-cm cells with >50% cover out of 100 cells in a 1 × 1-m vegetation frame (Wratten and Fry, 1980; Nellemann and Thomsen, 1994). We also recorded potential presence of Cladina rangiferina, Cladina mitis, Cladonia spp., Stereocaulon spp., Cetraria islandica, and Cetraria delisei, although most of these are located further down the snow gradient. Cover of Polytrichum piliferum, Racomitrium lanuginosum, Andreaea rupestris, Arctostaphylos spp., Empetrum nigrum, Loiseleuria procumbens, Betula nana, Juncus trifidus, Luzula spp., Poa spp., and Carex spp. were recorded in the same manner.

Average height of lichen was allocated to class 1 (0–1.5 cm), 2 (1.5–3.0 cm), or 3 (>3.0 cm) by measuring lichen height in five random points within the vegetation frame according to Nellemann et al. (2000). We calculated means from the five plots at each site. We used cover-biomass regressions for different lichen heights from Rondane (Nellemann et al., 2000) to assess relationships between lichen cover and biomass. Some of the lichens generally had low coverage (0–5%), but may depend upon erosion or grazing of the more dominant lichen species in order to colonize ridges. To develop a general tabular overview of the presence and absence of species at different extents of lichen cover, we divided lichen cover into four classes: >75% lichen cover; 50–74% lichen cover; 25–49% lichen cover, and 0–24% lichen cover. We then recorded the presence and absence of lichens on ridges according to this classification.

Snow depth and hardness were measured at each plot in 105 (64%) of the sites, using a ramsonde penetrometer (Skogland, 1978; Nellemann et al., 2000). Hardness (H_r ) was calculated using the following equation: H_r  =  (P_h × h_hd × n_hd) d ⁻¹ + Q, where P_h is the mass of the load (g), h_hd is the height of the hammer drop, n_hd is the number of hammer drops, d is the penetration into the snow cover (cm), and Q is the total mass of the ramsonde. We calculated an integrated ram hardness index (IRH) to derive a better measure of forage availability (Tucker et al., 1991; Vistnes et al., 2001), where IRH  =  H_r × d. Elevation was recorded using 1:50,000-scaled maps with a contour interval of 20 m, often in combination with GPS.

To evaluate the effect on lichen erosion resulting from potential differences in the sensitivity of lichens to grazing and cratering, we investigated seven ridges in southern Rondane grazed <24 h earlier by herds dominated by bulls. This is an area with an extensive lichen cover and a long history of very low grazing intensity (Dahl, 1956; Jordhøy and Skogland, 1985). At each of the seven ridges, five craters were selected randomly located >5 m apart. Lichen cover on ground in the crater was measured using the vegetation frame as described above, while lichen fragments in snow were collected within a 2-m radius around each crater. The fragments were then sorted by species, and the volume of each species was measured in a 200-mL cup in field. For comparison purposes, volume of lichen fragments in snow and cover of lichen on ground was converted to percent of total lichen, as lichen cover is closely correlated to lichen volume and biomass (Nellemann, 1996; Nellemann et al., 2000). By using sites grazed mainly by bulls, we avoided the effect of calves and juveniles grazing extensively on lichens kicked up by older animals around craters. During late winter, the bulls, having lost their antlers and thus unable to defend craters against parturient females, tend to graze in other areas than female-calf groups (Espmark, 1964; Thing, 1977; Skogland, 1989; Holand et al., 2004).

Reindeer Observations

Data on reindeer density and corresponding lichen biomass for 12 different subregions were gathered from the studies of Nellemann (1996), Nellemann et al. (2000; 2001), Jordhøy et al. 2003, and Vistnes et al. (2004). Here, reindeer density was estimated using systematic aerial fixed-wing or ground surveys in winter, following contiguous 4 km wide transects. Fixed-wing surveys were used in Snøhetta, Nord-Ottadalen, northern Rondane and Nordfjella, while reindeer in central Rondane were studied using ground surveys following approximately the same method as for fixed-winged surveys. All reindeer observed were photographed and located using GPS or topographic maps, and the number of reindeer determined. Surveys were conducted one day each winter for 8 yr in Nordfjella (1986–1998) and Nord-Ottadalen (1974–1985), 11 yr in northern Rondane (1987–1997), 5 yr in central Rondane (1991–1996), and 14 yr in central Snøhetta (1975–2000).

Statistical Analyses

Statistical analyses were performed in Sigmastat (SPSS, 1997). Polynomial regression analysis was used to determine the correlation between snow depth, elevation, and reindeer density, respectively, versus lichen biomass. Lichen composition on recently grazed ridges was compared with lichen fragments in the snow using t-tests, except for Cetraria islandica and Alectoria ochroleuca, where a Mann-Whitney rank sum test was used since normality tests failed for these species. In all cases, P-values < 0.05 were considered statistically significant.

Results

Effects on Snow Conditions on Availability of Exposed Ridges

In 85% of sites where snow characteristics were measured, snow depths were below 5 cm, and correlation between snow depth and lichen biomass was therefore very low (R ²  =  0.020). This was mainly a result of using only windblown ridges for intensive sampling. No grazing was observed in any other terrain, where snow depths typically varied between 60 and 200 cm. Ram hardness was on average 8.2 ± 0.7 kg, and integrated ram hardness (IRH) on average 33.2 ± 4.0 kg cm on exposed ridges. All hardness values were below 28 kg (83% below 10 kg) and thus below values found on ridges preferred by reindeer (Skogland, 1978), except for one site with a hardness value of 49.3 kg. This site was excluded from further analyses. Snow conditions were apparently quite similar in all sites visited, reflected also in the low variance among exposed sites.

Effects of Elevation on Lichen Biomass

Biomass was correlated to elevation when including all sites (R ²  =  0.39, P < 0.001, n  =  163). To control for this, we included only sites 1100 to 1400 m a.s.l. in further analyses, where elevation only explained 18% of the variance (R ²  =  0.18, P < 0.001, n  =  127). The proportion of the three major lichen species was only weakly related to elevation within sites 1100 to 1400 m a.s.l. (Flavocetraria nivalis: R ²  =  0.18, P  =  0.003; Cladina stellaris: R ²  =  0.11, P  =  0.027, and Alectoria ochroleuca: R ²  =  0.014, P  =  0.450).

Effects of Reindeer Density on Lichen Biomass

Reindeer density and lichen biomass was well correlated across the regions investigated (R ²  =  0.81; Fig. 2a–b). Biomass of Flavocetraria nivalis was correlated to reindeer density (R ²  =  0.80; P  =  0.008; Fig. 2b). Biomass of the two other species were less closely related to reindeer density (Alectoria ochroleuca; R ²  =  0.36, P  =  0.227; Cladina stellaris; R ²  =  0.54, P  =  0.094).

Figure 2A–B Correlation between annual reindeer densities (reindeer km⁻² yr⁻¹): (a) total lichen biomass (g m⁻²) and (b) Flavocetraria nivalis. Rondane, Nord-Ottadalen, Snøhetta, and Nordfjella wild reindeer regions, Norway.

Effects of Reindeer Cratering on Lichen Composition

Lichen composition on recently grazed ridges (<24 h) differed significantly from lichen fragments left in the snow surrounding the craters for Flavocetraria nivalis and Cladina stellaris (Table 2). The volume of Flavocetraria nivalis was significantly higher on ridges compared to remaining lichen fragments in snow (P < 0.001). The volume of Cladina stellaris was significantly lower on ridges compared to the fragments found in snow (P < 0.001). There was no significant difference between the amount of Alectoria ochroleuca found on ridges and in snow (P  =  0.142). This field work was conducted in an area rich on lichen (average 595 g m⁻² ± 81, n  =  7), corresponding to a lichen cover of >75%.

Table 2 Proportion (%) of total lichen volume in snow or lichen cover on ridge ±SE for three grazed lichen species on seven sites with a long history of low grazing pressure in Rondane, April 2006.

Test results also showed that there was a significant difference for Cetraria islandica but not for Alectoria nigricans between the proportion of lichen remnants observed in the snow versus the proportion observed on the ground. However, volumes were small for these two species which probably explains why they were not recorded on the ridge using the vegetation frame method which requires >50% coverage of at least one 10 × 10 cm cell, while they were registered in small amounts through the collection of lichen fragments in snow.

Effects of Reindeer Density on Ridge Vegetation Composition

Areas with little or no record of grazing were completely dominated by 5- to 10-cm-thick mats of Cladina stellaris, Flavocetraria nivalis, and Alectoria ochroleuca, only penetrated by Betula nana (Table 3). Flavocetraria nivalis became increasingly dominant among the lichens with increasing grazing pressure, while Cladina stellaris rapidly declined even at mild grazing levels (50–74% lichen cover) becoming almost absent at a 60% lichen cover (Fig. 3). Further grazing reduced overall lichen cover, resulting in a gradual increase in bare ground (abiotic cover) on grazed sites (Fig. 4a). The increase in bare ground was however 5 to 20% lower than the extent of the removed lichen cover as a result of the spreading and colonization of other species (Fig. 4a–b). When investigating ridges with moderate to heavy grazing levels, other lichen species like Cladonia spp., Alectoria nigricans, Bryocaulon divergens, and Thamnolia vermicularis became present, as well as Umbilicaria spp. and Hypogymnia alpicola on small rocks formerly covered by heavy lichen mats.

Table 3 Presence and abundance of common plant species on ridges along a grazing gradient from near absence of grazing by wild reindeer (75–100% lichen cover) to heavily grazed sites (0–25% lichen cover; Nellemann et al., 2000, 2001; Vistnes et al., 2001, 2004). Wild reindeer winter habitat, Norway.

Figure 3 The relationship between total cover of lichens and decline in cover of Cladina stellaris with increasing grazing pressure. Rondane, Nord-Ottadalen, Snøhetta, and Nordfjella wild reindeer regions, Norway.

Figure 4A–B Relationship between total lichen cover: (a) cover of bare ground and (b) cover of graminoids (mainly Juncus trifidus). Rondane, Nord-Ottadalen, Snøhetta, and Nordfjella wild reindeer regions, Norway.

Discussion

Effects of Snow, Terrain, and Elevation on Lichen Distribution

Snow can pose a major barrier to reindeer food sources in winter, determining which parts of the range are available for grazing (Pruitt, 1959; Fancy and White, 1985; Adamczewski et al., 1988; Collins and Smith, 1991). In addition, lichen biomass and composition may vary with elevation (Dahl, 1956; Arseneau et al., 1997; Grytnes et al., 1999; Bruun et al., 2006) and microtopography (Nellemann et al., 2000; Bruun et al., 2006). Indeed, Cladina stellaris tends to grow in areas with a slightly greater snow cover than Flavocetraria nivalis, but this is true mainly farther down the ridge where this species can be observed with other Cladina species (Dahl, 1956). To avoid any bias from this, we deliberately confined our sampling exclusively to lichen heath ridges with very shallow snow cover and no larger coverage of Cladina rangiferina, Cladina arbuscula, or Cladina mitis.

Given this limited range of variation in snow cover, elevation, and terrain, the second most important factor influencing lichen composition and biomass is probably grazing intensity. Optimal-foraging theory predicts that animals foraging in a patchy landscape will choose forage-rich patches, often estimated by protein or energy content, over poor patches (MacArthur and Pianka, 1966; Berteaux et al., 1998). Free-ranging animals are, however, also influenced by stochastically varying environments when making their foraging decisions (Schluter, 1981; Mangel and Clark, 1986). In late winter, ridge crests may be the only vegetation type that is not completely covered with snow (Adamczewski et al., 1988). Although reindeer are excellent diggers in snow, they will forage on wind-blown ridges and bluffs with softer and more shallow snow than what is average at the general site (LaPerriere and Lent, 1977; Collins and Smith, 1991; Johnson et al., 2001) to reduce energy expenditure. Lichens may thus be almost completely removed from the top of wind-blown ridges, and still be abundant at the snow-covered sides of the ridges only a few meters away (Nellemann et al., 2000).

Lichens as Forage in Winter

Reducing unnecessary digging in deep or hard snow is vital during winter when forage is limited. This is particularly important as lichens are rich on readily digestible carbohydrates, but low on proteins (Helle, 1984; Svihus and Holand, 2000). Their content of some 2–5% crude protein (except for 7–8% in Stereocaulon spp) is below what is needed for maintenance (Staaland et al., 1983; Garmo, 1986; Nieminen and Heiskari, 1988; Parker et al., 2005). Even with a recycling of nitrogen in urea (Hove and Jacobsen, 1975) and reduced appetite in winter (Pösö, 2005), Rangifer will most often suffer from a protein deficiency in winter, the nitrogen level will be below the requirements of rumen bacteria, and digestibility will be reduced (Huot, 1989; Gerhart et al., 1996). An additional negative effect is that intake of digestible carbohydrates, found in lichens, will increase the microbial nitrogen requirement and thus the loss of fecal nitrogen (Van Soest, 1994). Probably to increase nitrogen intake, reindeer commonly eat a varied diet also consisting of more protein-rich grasses like Deschampsia flexuosa (Helle, 1984; Danell et al., 1994; Aagnes et al., 1995), even when there is no shortage of lichens.

Effects of Grazing and Cratering on Lichen Composition

The reduction of Cladina stellaris with increased grazing (Tables 2, 3) indicated that this is a species heavily used by reindeer when available, and that it is easily eroded (Arseneault et al., 1997; den Herder et al., 2003; Boudreau and Payette, 2004a). Several studies have also documented that reindeer prefer Cladina stellaris to lichen species such as Stereocaulon paschale, and prefer lichens above moss and grass (Holleman and Luick, 1977; Danell et al., 1994). These studies did however not include Flavocetraria nivalis. Storheier et al. (2002) found a higher digestibility of Flavocetraria nivalis (70%) than of Cladina stellaris (50%), and Svihus and Holand (2000) found less soluble fiber and glucose in Cladina stellaris than in Flavocetraria nivalis. Cladina stellaris however had higher total monosaccharide content than Flavocetraria nivalis (Svihus and Holand, 2000).

Although our results seemed to indicate that Cladina stellaris was preferred above Flavocetraria nivalis, as the first disappeared early with grazing, this may also be explained by alternative or complimentary hypotheses. Gaare and Skogland (1975) found that reindeer had a very low preference of Cladina stellaris, even though it made up the largest volume of biomass removed from the ridges. They estimated a spillage factor of 10, and concluded that the considerable waste of Cladina stellaris largely must have been caused by cratering activity. Indeed, several studies have shown that Cladina stellaris is highly sensitive to grazing and is easily eroded (Arseneault et al., 1997; den Herder et al., 2003; Boudreau and Payette, 2004a). These results correspond with our comparison of lichen on ridges with lichen fragments in the snow removed through cratering, as well as the rapid decline in this species along the grazing gradient. The reason why Cladina stellaris disappears rapidly with grazing is likely caused by the different morphology of the two species. The Cladina stellaris thallus is easily removed in its entirety in big lumps, whereas the Flavocetraria nivalis thallus is more attached to the ground and is gradually cut down when grazed. It may therefore be more energy efficient for reindeer to graze lumps of Cladina stellaris than Flavocetraria nivalis. As we only included sites grazed by bulls mainly, we also avoided the effect of animals with a lower social status (such as calves) influencing the observations through secondary grazing on lichens fragments in the snow or in craters dug by older animals (Skogland, 1989).

Alectoria ochroleuca is a less studied species although it often is dominant in volume. Arseneault et al. (1997) suggested that this species was avoided by caribou. Gaare (1968) observed that Alectoria ochroleuca had almost entirely disappeared from grazed sites although it was not found in rumen samples, and concluded that it must have been removed through trampling alone. Our results imply however that it also might have been grazed, as few fragments were found at newly grazed sites. It has also been documented that Alectoria ochroleuca is rich on soluble fiber and glucose (Svihus and Holand, 2000). Oksanen and Virtanen (1995) concluded that reindeer had low preference for Alectoria ochroleuca as it holds high levels of lichenic acids, but that it still may be grazed when other species are unavailable.

Colonization and Vegetation Change on Grazed Ridges

Grazing has profound effects on the composition of lichens, but also on the composition and colonization of other species on the ridges through the removal of dominant species and the exposure of bare soil (Olofsson, 2001; 2006). Within our study areas, some ranges have been nearly ungrazed for at least a century (Dahl, 1956; Jordhøy and Skogland, 1985), while others have experienced varying grazing pressure for millennia, also including heavy grazing for the past decades (Barth 1996; Skogland, 1986; Vistnes et al., 2004). This has resulted in a gradient from a near monoculture of Cladina stellaris, Alectoria ochroleuca, and Flavocetraria nivalis (Dahl, 1956) on ridges with little or no grazing, to moderately grazed ridges with higher species diversity and heavily grazed ridges exposed to erosion. The high proportion of Cladina stellaris in the snow around craters suggests high vulnerability to erosion and grazing, and was also well reflected in coverage of this species along the gradient of lichen cover. Moderate grazing by the Rondane herd is reflected in the steep decline in Cladina stellaris (Nellemann et al., 2000; Boudreau and Payette, 2004a). In other parts of our study areas where ranges were heavily grazed in the 1960 to 1980s, Cladina stellaris is still absent from exposed ridges (Henry and Gunn, 1991; Nellemann, 1996; Vistnes et al., 2004).

Most interesting however, is the transition in vegetation observed along these grazing gradients (Fig. 5). When lichen mats completely covered the ground, only penetrated by Betula nana (Oksanen and Virtanen, 1995), removal of the lichens by cratering, grazing, and trampling exposed bare ground. This bare ground, especially when reaching levels of 30 to 40% cover, was gradually colonized by mosses and crustose lichens (Boudreau and Payette, 2004b). The observed 10 to 25% increase in new plant cover following removal of lichens by grazing was likely a result of lowered competition among remaining species, as well as colonization of bryophytes like Polytrichum piliferum, Racomitrium lanuginosum, and Andreaea rupestris, dwarf shrubs like Arctostaphylos spp., Empetrum nigrum, and Loiseleuria procumbens and rushes like Juncus trifidus (Fig. 4b, Fig. 5; Table 2). The colonization of graminoids was however highly variable, and most prominent for the most heavily grazed sites, possibly being an effect of fertilization from faeces and urine given that these small narrow ridges are used repeatedly by many animals (Olofsson et al., 2001, 2004b; Olofsson, 2006). There appeared to be a slight increase in dwarf shrubs, in particular of Arctostaphylos spp. and Loiseleuria procumbens, while Empetrum nigrum did not increase very much (Olofsson et al., 2005). At the most heavily grazed sites, coverage remained low also of dwarf shrubs, likely because they are frequently pulled out of the ground by reindeer when grazing or snow conditions are marginal. Here, only a few graminoids established, particularly the rush Juncus trifidus. Even mosses had low coverage when abiotic ground covered up to 90%, possibly a result of grazing and trampling (van der Wal and Brooker, 2004). Along with mosses, typically Polytrichum piliferum (Fig. 5) and Andreaea rupestris, we also observed a colonization of moderately grazed ridges by other lichens, particularly of crustose lichens, Cladonia spp., A. nigricans, Bryocaulon divergens, and Thamnolia vermicularis, thus increasing diversity of both lichens and mosses compared to sites with low or no grazing pressure (Austrheim and Eriksson, 2001; Olofsson et al., 2001; den Herder et al., 2003; Boudreau and Payette, 2004b; Eskelinen and Oksanen, 2006).

Figure 5 Impacts of grazing: (a–c) near absence of grazing has led to a 5- to 15-cm-thick monoculture layer of only Cladina stellaris, Alectoria ochroleucha, and Flavocetraria nivalis; (d) moderate grazing where small “white” rocks not yet overgrown with Rhizocarpon spp. or Umbilicaria spp. suggest removal of fruticose lichens by grazing in the past couple of decades; and (e–f) high grazing pressure with a gradual colonization by crustose lichens, Polytrichum piliferum, Andreaea rupestris, Loiseleura procumbens, and a few persistent Flavocetraria nivalis.

In conclusion, moderate grazing on wind-blown ridges in winter reduced overall biomass, but increased diversity of both mosses, lichens, graminoids and dwarf shrubs, possibly by exposing bare ground, reducing competition, and increasing nitrogen turnover through more exposure to the sun and addition of feces and urine. Very heavy grazing and trampling may in a short term be beneficial to a range of colonizing species, but in the long term destroy vegetation cover and result in erosion on exposed ridges.