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- Materials and Methods
Species’ range boundaries often show a close association with particular climatic variables (Pigott, 1968, 1992; Conolly & Dahl, 1970; Tofts, 1999). This observation is supported by both correlative approaches linking distributional limits with isometric lines of climate (for example; Salisbury, 1926, Conolly & Dahl, 1970) and identification of the principal factors that limit the spread of particular species (Pigott, 1968; Pigott & Huntley, 1981). Low temperatures may limit poleward spread through their actions on both the vegetative (Woodward, 1990, 1997) and reproductive phases of plant growth (Pigott, 1968; Pigott & Huntley, 1981; Woodward, 1990). The factors limiting spread in the equatorial direction are less clear. High temperature (Conolly & Dahl, 1970) and water availability (Pigott & Pigott, 1993) have been implicated and competitive exclusion may play a key role (Woodward, 1996).
The favourability of a species’ environment is expected to decline from the core to the periphery of a species’ range (Brown, 1984), based on the observation that environmental factors frequently change in a clinal manner (Endler, 1977). This pattern is expected to result in a decline in the favourability of a species’ typical habitat toward the range edge and, consequently, a reduction both in the abundance of individuals within a population and the density of populations within an area (Hengeveld & Haeck, 1982; Brown, 1984). Habitat at the geographical range margins is expected to be ecologically marginal for many species (Lawton, 1993, Lesica & Allendorf, 1995). This is predicted to result in a species occurring in atypical habitat (and hence different plant communities; Crozier & Boerner, 1984; Dibble et al., 1999) in peripheral areas, where the impact of decreased environmental favourability is reduced (Lesica & Allendorf, 1995). Declining environmental favourability is expected to result in a decrease of both plant growth and reproduction toward species’ range boundaries (Parsons, 1991).
Many species exhibit a decline in seed production toward their range boundary (Pigott, 1968; Pigott & Huntley, 1981; Reinartz, 1984b; Eckert & Barrett, 1993; García et al., 2000; Dorken & Eckert, 2001). The reproductive phase of the plant lifecycle shows particular sensitivity to climate (Marshall, 1968; Pigott, 1968; Pigott & Huntley, 1981; Houle & Filion, 1993; Despland & Houle, 1997; Woodward, 1997; García et al., 2000). Variation in vegetative characters such as plant size (Marshall, 1968; Clevering et al., 2001) and differential allocation to above- and below-ground organs (Benowicz et al., 2000) toward a species’ range limit have also been reported. Differences in plant size may ultimately be reflected in the reproductive success of the plant (Reinartz, 1984a,b; Primack, 1987; Wesselingh et al., 1997).
Many studies have reported variation in plant characters along altitudinal or latitudinal gradients (Clausen et al., 1940; Pigott, 1968; Lacey, 1984; 1988; Aizen & Woodcock, 1992; Winn & Gross, 1993; Wesselingh et al., 1994; Jonas & Geber, 1999). Although investigation into the effects of reaching a species periphery is often inherent in studies conducted over latitudinal gradients, there is a bias toward investigating the poleward periphery of a species distribution. Studies that record trait variation toward the equatorial periphery or across the entire geographical range of a species are relatively rare (but see Reinartz, 1984a,b; García et al., 2000). Furthermore, studies usually concentrate on a few closely related traits and can therefore present only a fragmented view of plant performance across a species geographical range. Seed production, for example, may represent an integrated measure of plant productivity. A reduction in seed production may result from a specific physiological limitation on seed development (Pigott & Huntley, 1981), or an overall reduction in plant growth (Reinartz, 1984a,b; Primack, 1987). This study aims to present a more extensive view of variation in plant traits from the core to the periphery of a species’ range.
We report trait variation across the UK geographical range of three Cirsium species (C. acaule, C. arvense and C. heterophyllum, Fig. 1). These are perennial, insect-pollinated species that produce wind-dispersed seeds. In addition to reproduction by seed, all reproduce vegetatively by the production of new shoots from underground root and stem tissue (Pigott, 1968; Moore, 1975; Clapham et al., 1981; Grime et al., 1989). Cirsium acaule reaches a northern distributional limit in the UK, in Europe it extends from northern England and Estonia southwards to southern Spain, Serbia and south-east Russia (Tutin et al., 1976). Cirsium heterophyllum occurs at low altitudes in northern Europe and the eastern part of the former USSR, and reaches a southern distributional limit in the UK (Fig. 1). High altitude populations of C. heterophyllum occur in the mountain ranges of Europe, southwards to the Pyrenees and Transylvania (Tutin et al., 1976). Cirsium arvense is a widespread species used for comparison. It occurs almost throughout Europe and is absent only from Svalbard in the extreme north and Crete and the Azores in the south (Tutin et al., 1976). Previous studies have reported a close association between both the northern range boundary of C. acaule and the southern boundary of C. heterophyllum with isotherms of summer temperature (Pigott, 1968; Conolly & Dahl, 1970), implicating climate as a major factor in determining the distribution of these species.
This work will build on previous studies that report geographical patterns in single traits within single species. It will allow both interspecific and intraspecific comparison of trait patterns by reporting intraspecific geographical variation in key areas of population distribution, community composition, morphology and seed production within three congeneric species. A companion paper (Jump et al., 2003) will presents geographical patterns in the population genetic structure of these species.
Given the predicted decline in environmental favourability, this study aims to determine whether gradients in morphological characters, seed production, population density and abundance occur from the core to the periphery of C. acaule and C. heterophyllum in the UK and whether geographically peripheral populations of these species occur in atypical plant communities.
Materials and Methods
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- Materials and Methods
As this work will investigate potential north–south clines in characters in these species, latitude will be used as a proxy for distance from the core of the species distribution. Latitude is a good proxy for the action of many factors such as radiation balance, length of growing season and the frequency of frost events. Indeed, Valentini et al. (2000) reported latitude to be a better correlate of ecosystem respiration than any single factor they tested (including mean annual temperature, precipitation and elevation) when investigating forest carbon balance. Furthermore, investigating core–periphery patterns in species has the inherent problem that range edges are extremely difficult to define reliably (Blackburn et al., 1999). Thus, when investigating north–south clines, latitude is a surrogate measure that provides both an indication of the position of populations and the distance between them in the absence of a reliable and repeatable method of defining a species range edge.
Surveys were carried out during July and August 2000 within the populations listed in Table 1. Cirsium acaule populations were surveyed only on slopes facing south to south-east since Pigott (1968) reported great sensitivity of seed production to aspect in this species. In this species, comparing data from sites of different aspect could potentially obscure any latitudinal pattern that may occur within similar populations. Populations of C. heterophyllum and C. arvense were surveyed on level ground.
Table 1. Location of study populations
|Cirsium acaule||Cirsium heterophyllum||Cirsium arvense|
|Site code||Site location||Altitude (m)||Site code||Site location||Altitude (m)||Site code||Site location||Altitude (m)|
|11||50.587°N 2.032°W|| 70||51||53.214°N 1.765°W||280||11||50.677°N 2.644°W||130|
|12||50.672°N 2.587°W||150||52||53.231°N 1.844°W||320||12||50.684°N 2.655°W||140|
|13||50.630°N 1.969°W|| 80||53||53.241°N 1.780°W||290||31||51.439°N 2.401°W||180|
|21||51.209°N 2.092°W||130||54||53.166°N 1.879°W||270||32||51.430°N 2.404°W||230|
|22||51.262°N 2.034°W||160||61||54.408°N 2.337°W||220||41||51.839°N 2.107°W||170|
|23||51.269°N 2.023°W||130||62||54.439°N 2.587°W||170||42||51.862°N 2.071°W||260|
|31||51.447°N 2.401°W||180||63||54.862°N 2.508°W||200||51||53.214°N 1.765°W||280|
|32||51.430°N 2.404°W||230||64||54.447°N 2.387°W||270||52||53.145°N 1.728°W||260|
|33||51.327°N 2.791°W||150||71||56.490°N 4.748°W||200||61||54.521°N 2.497°W||200|
|41||51.842°N 2.107°W||190||72||56.400°N 5.213°W|| 80||62||54.527°N 2.329°W||160|
|42||51.865°N 2.073°W||260||73||56.321°N 3.685°W||100||71||57.321°N 4.363°W||240|
|43||51.842°N 1.996°W||210||81||57.101°N 3.987°W||260||72||57.101°N 3.987°W||260|
|51||53.262°N 1.733°W||320||82||57.015°N 4.162°W||290|| || || |
|52||53.138°N 1.714°W||250||83||57.327°N 3.021°W||320|| || || |
| || || ||84||57.420°N 2.627°W ||230|| || || |
| || || ||91||57.990°N 4.814°W ||150|| || || |
| || || ||92||58.243°N 5.177°W || 50|| || || |
| || || ||93||57.753°N 5.011°W ||200|| || || |
Population density was determined by comparing the 2 × 2 km (tetrad) Botanical Society of the British Isles (BSBI) Monitoring Scheme survey data with the 10 × 10 km (hectad) survey data of the Atlas of Flowering Plants and Ferns of Britain and Ireland (Preston et al., 2002). The BSBI Monitoring Scheme survey is a systematic survey that takes up to three tetrad subsamples from one in every nine (11%) of the hectads of the BSBI grid (see Rich & Woodruff, 1990, 1996). Since, from the Atlas survey, we know whether the species of interest occurs in the hectad being sampled, the density of populations of that species within that hectad is indicated by the number of tetrad samples of the monitoring scheme survey that record it. Thus, a decline in population frequency will be represented by a decline in the number of tetrads per hectad that include the species of interest.
A frequency score was calculated by dividing the number of tetrads per hectad containing the species of interest by the number of tetrad samples taken within that hectad. As tetrad samples have been taken only within hectads where the species of interest is known to occur, a score of 0 indicates lowest frequency within this hectad rather than absence. To reflect this, frequency scores were expressed on a scale ranging from 1 (least frequent) to 5.
Abundance was measured as the maximum density of individuals within a population, based on samples of randomly placed quadrats in the densest area of the population. For C. arvense and C. heterophyllum, abundance was recorded as the number of shoots within two 1 × 1 m quadrats at each site; for C. acaule abundance was based on the number of clumps rather than individual shoots and recorded from two 5 × 5 m quadrats. Quadrat size was larger for C. acaule because this species occurs as scattered individuals rather than the dense stands that are typical of C. arvense and C. heterophyllum.
Two community surveys were conducted in each population. Per cent shoot frequency of each species present was calculated based on presence in each of 25 cells of a 50 cm × 50 cm strung quadrat (Goldsmith et al., 1986). Quadrats were placed randomly within the densest area of the population.
Morphological traits and seed production
The traits measured in each species are listed in Table 2. Owing to access agreements made with conservation authorities in the Peak District National Park, UK, it was not possible to perform any destructive analysis (e.g. biomass) on C. acaule or C. heterophyllum in this area. Consequently, with the exception of the collection of seed heads, all measures were nondestructive. Collection of seed heads was restricted to less than 30% of those produced by each population studied.
Table 2. Morphological and seed traits measured in the Cirsium species investigated
|Species||Characters measured (n = 30)|
|All species||Maximum length and width of youngest fully expanded leaf (excluding petiole)|
|Total filled seed mass per capitulum|
|Percentage of population failing to set seed|
|Cirsium acaule only||Maximum clump diameter|
|Cirsium arvense and C. heterophyllum only||Height at flowering|
|Number of flowers per plant|
Within each population, 30 plants were chosen at random and the traits measured as listed in Table 2. Cirsium acaule rarely produces a flowering stem, flowering instead within the rosette. Clump diameter was used as an additional measure of plant growth (as opposed to height) in this species. The total number of capitula produced per plant was not recorded for C. acaule because of the indeterminate flowering of populations of this species within a season. The ratio leaf length to leaf width was used as an indication of leaf shape, while leaf length indicated leaf size (Mooney & Billings, 1961; Rochow, 1970).
To assess seed production, 30 ripe but not dehiscent capitula were collected at random within each population. In C. arvense these were chosen only from female flower heads (Moore, 1975; Heimann & Cussans, 1996), in C. heterophyllum the terminal capitulum was selected from the flowering stem of each plant. Capitula were air dried in paper envelopes for 1 month before deseeding. Seeds were extracted from each capitulum by removing the pappus material and seeds and rubbing this across a soil sieve (4 mm mesh). The seeds collected were then cleaned of debris and sorted by hand using a hand-lens to separate entire, filled seed from unfilled seeds and those damaged by insect predation. Damage due to seed predation was scored between 0 and 4 for each capitulum. Total filled seed mass per capitulum was recorded.
Community data were analysed using a combination of classification and ordination methods. Such methods are usually used to identify particular phytosociological groups, however, our aim in the analysis of these data was to identify outlying samples (rather than the main clusters) to determine whether the peripheral populations of C. acaule and C. heterophyllum occur in atypical communities. A potential problem with this approach is that different methods for the analysis of community data are likely to deal with outlying samples in different ways (Gauch & Whittaker, 1981). The most informative approach is thus to use several different methods of analysis on the same data set and compare the results to get a more comprehensive view of the data structure (Kent & Ballard, 1988).
Community data were classified using the agglomerative increase sum of squares method, followed by calculation of sample proximities based on squared Euclidean distance, using the program clustangraphics (Wishart, 1999). An additional divisive classification was produced using the default parameters of the programme twinspan (Hill, 1979a; Malloch, 1999). Community ordination (detrended correspondence analysis, DCA) was performed using the default parameters of the programme decorana (Hill, 1979b; Malloch, 1999). See Kent & Coker (1992) for a detailed description of these techniques. The authors of these programmes (M. Hill and A. Wishart) were contacted to confirm the validity of this approach.
Population density and abundance, seed production and morphological characters were regressed against latitude using sigmaplot 2001 for Windows v7 (SPSS Inc. Chicago, IL, USA).
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Hengeveld & Haeck (1982) proposed the general biogeographical rule that species become rarer toward their range margins, independent of the spatial scale of observation. They predicted that declining environmental favourability with increasing distance from the core of a species range would lead not only to a decrease in favourable habitat patches, but also a decline in the favourability of any patches that occur; thereby leading to a decline in both density and abundance (Brown, 1984). Although population density declines approaching the periphery of both C. acaule and C. heterophyllum, only in C. heterophyllum is this accompanied by a decline in abundance within populations; C. acaule does not fit the pattern of parallel decline in abundance predicted by both Hengeveld & Haeck (1982) and Brown (1984). Sagarin & Gaines (2002) found that only 39% of the studies that they reviewed supported the predicted decline in abundance. Cirsium acaule may favour an alternative pattern discounted by Hengeveld & Haeck (1982), that the number of favourable habitat patches may decline approaching the range boundary but that abundance within them remains the same – a pattern also reported by Pérez-Tris et al. (2000). This may, in some part, be explained by the great sensitivity of C. acaule to summer irradiance (Pigott, 1968) acting more in terms of a presence/absence (threshold) effect in this species rather than the gradual decline predicted to result from the processes described by Brown (1984).
There is no support from community surveys of C. acaule or C. heterophyllum for the prediction that peripheral populations will occur in atypical habitat. There is only limited support for this prediction in the literature. For example, Fernald (1925) described a mixing of species typical of northern North America with those typical of southern states of the USA, in rare communities at the edge of their geographical ranges. Barden (2000) described southern peripheral populations of the common shrub Quercus ilicifolia, which occur in a rare community type not seen in other areas of the species range. However, since species are often found in a greater variety of habitat types in core rather than peripheral areas of their distribution (Hall et al., 1992; Pérez-Tris et al., 2000) it may be more likely that, at the periphery, they will be restricted to only the most favourable of these, rather than occurring in novel habitat unoccupied elsewhere in the range.
Despite the general absence of latitudinal patterns of morphological traits in these species, there is a significant increase in clump size in C. acaule approaching the periphery of this species. This trait is not comparable with plant size traits measured in the other Cirsium species, since, in C. acaule, clump size refers to the size of individual genets rather than the size of ramets measured as morphological traits for the other species. It may be more accurate to view clump size as an indicator of vegetative reproduction rather than plant size. If so, this raises questions as to whether this may occur as a result of reproductive assurance (Pannell & Barrett, 1998) in this species, given that vegetative offspring may have a greater chance of survival in peripheral populations compared with plants produced by seed (Eckert & Barrett, 1993).
When considered alongside the absence of patterns in morphological traits, the decline in seed production approaching the range edge of C. acaule and C. heterophyllum suggests that reduced reproductive success rather than vegetative survival may limit the geographical distribution of these species in the UK. This pattern is in agreement with that described for many plant species (Pigott & Huntley, 1981; Reinartz, 1984b; Eckert & Barrett, 1993; García et al., 2000; Dorken & Eckert, 2001). Climate is implicated in determining the distribution of C. acaule and C. heterophyllum (Pigott, 1968; Conolly & Dahl, 1970), Pigott (1968) noted a reduction in seed production in C. acaule at its northern limit linked to the reduced heat sum gained by the capitula of northern populations. Despite this, some viable seed is produced (indicated by the presence of seedlings in both peripheral populations in 2000). Although a decline in seed production approaching the range edge is reported frequently, recruitment by seed is likely in peripheral populations since pronounced interannual variation in both climate and seed production occurs (Pigott, 1968; Pigott & Huntley, 1981; Houle & Filion, 1993; Despland & Houle, 1997; Woodward, 1997). However, production of viable seed does not necessarily result in the expansion of a species’ geographical range, since recruitment depends on seed production, seedling establishment and seedling survival (Pigott, 1992; Dorken & Eckert, 2001).
In species that combine seed production with vegetative spread, clonal reproduction allows populations to persist in the absence of recruitment by seed (Ellstrand & Roose, 1987; McLellan et al., 1997; Dorken & Eckert, 2001). Since each of the species investigated here employs both these means of reproduction, the marked reduction in seed production does not imply that populations should be unable to persist at the range edge. However, the founding of new populations of these species will be largely dependent on the dispersal of viable seed and subsequent plant establishment. If the decline in the density of populations reported here is interpreted as indicating a decline in density of favourable habitat patches (Brown, 1984), range expansion may be limited by the combined effects of reduced seed production and decreased probability of successful dispersal to (increasingly distant) favourable sites. Levels of seed production (and hence seed dispersal) at the periphery may be below those required for the successful establishment of new populations (Primack & Miao, 1992) despite the production of some viable seed by existing populations.
Environmental stress levels are expected to rise toward a species periphery as a result of declining environmental favourability (Parsons, 1991; Hall et al., 1992). A predicted consequence of this is a decrease in energy available for growth and reproduction approaching the range edge and hence a decline in plant size and the production of seed. The geographical limit for vegetative survival and that for the production of viable seed may, however, be determined by very different environmental conditions (Woodward, 1997) and sometimes widely separated in space (Woodward, 1990). At geographical limits where species can grow and complete a normal life cycle, successful regeneration is not guaranteed even if viable seed is produced; thus, the realized range of a species in the natural environment may differ from that which it might theoretically occupy based on vegetative survival (Pigott, 1992). The proposed effect of stress might not be seen on plant growth if a species’ distribution is limited by poor reproduction. The range limits of C. acaule and C. heterophyllum may result from reduced seed production acting in combination with a decrease in the availability of favourable habitat patches; the combined effect of these factors may make the establishment of new populations unlikely. These species are therefore likely to be absent from the region that is expected to be highest in stress (due to poor reproduction), despite the fact that they might survive vegetatively in this area. Consequently, since the effects of declining environmental favourability are more likely to be detected through reduced reproduction, the proposed effects of stress may not be detectable as a reduction in growth in the natural environment.