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Article

The Effect of Visitors on the Properties of Vegetation of Calcareous Grasslands in the Context of Width and Distances from Tourist Trails

by
Kinga Kostrakiewicz-Gierałt
1,*,
Artur Pliszko
2 and
Katarzyna Gmyrek-Gołąb
1
1
Department of Tourism Geography and Ecology, Institute of Tourism, Faculty of Tourism and Recreation, University of Physical Education in Cracow, 31-571 Cracow, Poland
2
Department of Taxonomy, Phytogeography, and Palaeobotany, Institute of Botany, Faculty of Biology, Jagiellonian University, 30-387 Cracow, Poland
*
Author to whom correspondence should be addressed.
Sustainability 2020, 12(2), 454; https://doi.org/10.3390/su12020454
Submission received: 16 December 2019 / Revised: 3 January 2020 / Accepted: 4 January 2020 / Published: 7 January 2020
(This article belongs to the Special Issue Sustainable Tourism - Ways to Counteract the Negative Effects of Overtourism at Tourist Attractions and Destinations)
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Abstract

:
Over the last decades, valuable natural areas considered as zones of silence and rest have been increasingly struggling with the problem of mass tourism. In this study, an investigation of the effect of visitors on the properties of vegetation of calcareous grasslands in the context of width and distances from tourist trails is performed. The study was conducted in seven localities in Cracow (southern Poland) involving calcareous grasslands impacted by tourist trails. The results show that the lower height of plants, the greater number of species and the greater percentage of plant cover damaged by trampling in plots located close to the edge of tourist trails, as well as lower total plant cover and greater mean cover-abundance degree per species along narrow pathways. The dominance of meadow and grassland species, as well as the prevalence of native species, suggests that the composition of the examined vegetation has not been drastically changed. In the majority of the study plots, the dominance of hemicryptophytes and chamaephytes, inconsiderable share of phanerophytes and therophytes, as well as the low share of geophytes, were observed. The infrequent occurrence of species presenting Bidens dispersal type along narrow pathways, as well as in plots located close to the edge of tourist trails, suggests low external transport of epizoochorous seeds by passing people, while the prevalence of species presenting Cornus type in plots located away from the edge of tourist trails might be the effect of dung deposition by animals.

1. Introduction

The phenomenon of overtourism, which is understood as the opposite of sustainable tourism, has been known and described so far mainly in the urban areas (e.g., [1,2,3,4]). However, it is also beginning to appear in regions considered as zones of silence and rest [5,6,7]. According to numerous authors [8,9,10,11,12,13,14,15,16], valuable natural areas are increasingly struggling with the problem of mass tourism. The negative consequences of the excessive tourist traffic represented, among others, by excessive water intake and sewage production, waste generation, noise, increased probability of fire initiation, synanthropisation of flora and fauna, scaring away of animals, as well as changes in the structure of biocoenoses were repeatedly noted in protected areas. Another consequence of excessive tourist traffic is trampling, which leads to the creation of informal trails. The trampling might contribute to changes in vegetation through mechanical damage of plants and species loss [17,18], as well as the influence on seed germination, seedling establishment, growth functions after establishment, vigour and biomass production, as well as flowering and fruiting [19]. Moreover, the trampling might improve the dissemination of diaspores over long distances [20,21], particularly the dispersal of non-native taxa [22].
To date, investigations of the impact of intensity, frequency and season of human trampling on vegetation properties and traits of selected plants have been the main focus of numerous experimental research on sustainable use of natural habitats for recreation in many different habitat types around the world e.g., [23,24,25,26,27,28,29,30]. In the last decades, an increase in the number ofstudies focusing on the impact of trampling and tourist dispersion on the surrounding environment has been observed. Generally, such studies have been carried out in areas protected by law or in hot spots of biodiversity e.g., [29,31,32,33,34], and mostly they concentrated on the causes and consequences of tourist dispersion around the trails. At the same time, investigations of the impact of pathway dimensions and/or distance from pathway edge on adjacent vegetation traits e.g., species richness and diversity, height of plants and proportions of species representing different life forms were carried out in forests [35,36,37,38,39,40] and scrublands [41], as well as in open habitats such as mires and feldmark vegetation [42], heaths [38,43], meadows [38] and dunes [44]. Despite the growing interest in the aforementioned issue, the current state of knowledge is still insufficient, especially in the case of semi-natural calcareous grasslands (Festuco-Brometea), which are nowadays considered as one of the most endangered plant communities in Europe, covered by the Natura 2000 network [45].
In this study, we focused on the impact of width of tourist pathways and distance from pathways on (i) plant cover features i.e., height of the tallest plant shoot, species abundance, damaged plant cover percentage by trampling, total plant cover percentage, cover-abundance degree of particular species, and (ii) occurrence of species presenting different habitat affiliations, dispersal modes, life forms and origin (native or alien status in the flora). We aimed to test the hypotheses that (i) the height of plants is lower in plots located near pathways than that in plots located away from pathways, (ii) the percentage of plant cover damaged by trampling is higher in plots located near pathways than that in plots located away from pathways, (iii) the percentage of plant cover damaged by trampling is higher along narrow pathways than that along wide pathways, (iv) the number of species is higher in plots located near pathways than that in plots located away from pathways, and (v) the spectra of habitat affiliation, life form, dispersal mode, and origin of species occurring in plant cover vary significantly among plots situated along pathways with different width, as well as among plots located in diverse distance from tourist trails.

2. Materials and Methods

2.1. Location of the Study Sites

Seven study sites located in the southwest part of Cracow (southern Poland) have been selected: Bogucianka, Fort Bodzów, Górka Pychowicka, Tyniec, Uroczysko Kowadza, Uroczysko Wielkanoc and Zakrzówek. All the study sites are situated on limestone hills within the Bielańsko-Tyniecki Landscape Park (BTPK), a part of the Jurassic Landscape Parks Complex, which constitutes a valuable area protected by law due to its excellent natural, cultural and historical properties.
The vegetation is mainly represented by beech and hornbeam forests from the Querco-Fagetea class and by calcareous grasslands from the Festuco-Brometea class. In calcareous grasslands the following vascular plants are commonly found: Achillea millefolium L., Coronilla varia L., Dianthus carthusianorum L., Echium vulgare L., Euphorbia cyparissias L., Fragaria viridis Weston, Plantago media L., Plantago lanceolata L., Potentilla arenaria Borkh, Thymus austriacus Bernh. and T. glabrescens Willd. In most of the study sites, the plants did not create the continuous cover and gaps in the turf were observed. The study sites are influenced by similar climatic conditions. According to Matuszko and Piotrowicz [46], the mean annual air temperature achieves 8.6 °C, while the average annual sum of actual sunshine duration amounts to 1539.3 h. The average annual relative humidity amounts to 78%, the highest average monthly values during the year occur in autumn and winter, during spring the humidity drops quickly and achieves the minimum in April. The average annual number of dry days reaches 17.8 and they occur mainly in the warm half-year as single days or two-day periods. The atmospheric precipitation achieves ca. 690 mm and the peak of precipitations occurs in July.
Due to their location within the border of Cracow and easy access by public transport, all the study sites are exposed to the recreational activities of citizens and tourists. “The Cracow City Forest Trail” is a marked walking and cycling route leading, among others, through Bogucianka, Górka Pychowicka, Uroczysko Kowadza and Uroczysko Wielkanoc. Moreover, Perzanowska [47] pointed out that Fort Bodzów and Uroczysko Kowadza are perfect places suitable for outdoor recreation (Table 1).

2.2. The Overview of the Study Design and Characteristics of the Study Plots

In each location, two visitor-created (informal) pathways were selected: a narrow one (up to 50 cm in width) and a wide one (at least 115 cm in width) based on the assumption that the width of the path is positively correlated with the intensity of tourist traffic (Table 1). The narrow trail can be used by one person, while the wide trail allows at least two people to pass in one direction or to pass each other. The pairs of 1 × 1 m research plots were established along each pathway. The pairs were systematically distributed every 2 m (alternately on both sides of the pathway). Each pair consisted of a plot labelled CL situated close to the edge of the pathway at a distance of 10 cm, and a plot labelled FU located much further at a distance of 150 cm from the plot CL (Figure 1). The distance from the edge of the trail was chosen arbitrarily on the basis of the behavior of tourists. Plots CL were established in places often trampled by tourists to avoid the trail after rainfalls, when the surface is muddy and slippery. Plots FU were established at a greater distance from the trail where descending from the pathway is due to willingness of taking photographs, curiosity, repose, or other causes.
The measurements of the abiotic habitat conditions, which were tested in particular plots by using the handheld device BIOWIN, evidenced that light intensity ranged from 740.0 Lx to 2000.0 Lx, soil moisture ranged from 1.0 to 6.7, whereas soil pH was from 7.1 to 7.8 (Table 2). The ANOVA analysis of main effects evidenced that the values of light intensity were similar in both the narrow and wide patches, the soil moisture was significantly greater in the plots CL than in the plots FU (F = 9.85, p < 0.01), and the soil reaction achieved greater values in the plots located along the wide pathways than in the narrow ones (F = 10.30, p < 0.01).

2.3. The Field Trial

Field study was conducted in July 2019. The height of the tallest plant shoot from the ground level to the top of the stem was measured in each study plot using a folder tape. Within each plot, the total percentage of plant cover and the percentage of plant cover damaged by trampling were visually estimated using a cover-abundance scale with an interval of 5%. Furthermore, the vascular plant species growing in the herbaceous layer within each plot were inventoried. The seedlings and saplings were removed and determined according to Csapodý [48] and Muller [49]. The degree of cover-abundance of each species was visually estimated according to a scale of Braun-Blanquet [50]. The explication of particular points of scale is as follows:
  • -“+”- species covers less than 1% of the studied area,
  • -“1”- species covers 1–5% of the studied area,
  • -“2”- species covers 6–25% of the studied area,
  • -“3”- species covers 26–50% of the studied area,
  • -“4”- species covers 51–75% of the studied area,
  • -“5”- species covers 76–100% of the studied area.

2.4. The Species Groups

To assess the species response to tourist activities, we selected four traits (i.e., habitat affiliation, life form, native or alien status in the flora and mode of seed dispersal) that were “ecologically meaningful” in accordance with the ability to persist in the stressful conditions caused by man (trampling) and accompanying animals (ground browning, wallowing). The traits of particular vascular plant species evidenced in the plots are presented in Table A1.
Habitat affiliation was assigned according to Matuszkiewicz [51]. The species were assigned to (i) grassland species (occurring in calcareous grasslands from the Festuco-Brometea class, thermophilic fringe communities representing the Rhamno-Prunetea and Trifolio-Geranietea sanguinei classes, grasslands and heaths from the Nardo-Callunetea class, pioneering communities on mobile or poorly fixed screes Thlaspietea rotundifolii, rocky grasslands Seslerio-Festucion duriusculae, calamine grasslands Violetea calaminariae, sandy grasslands Koelerio glaucae-Corynephoretea canescentis), (ii) meadow species (occurring in communities representing the Molinio-Arrhenatheretea class), (iii) forest species (occurring in communities from the Querco-Fagetea class), and (iv) ruderal species (occurring in ruderal communities of perennial plants from the Artemisietea vulgaris class, nitrophilous communities of logging, trampled and ruderal areas from the Epilobietea angustifolii class, semi-ruderal xerothermic pioneer communities from the Agropyretea intermedio-repentis class, communities of arable fields Stellarietea mediae, segetal weeds community Papaveretum argemones, and annual plant and biennial ruderal plant communities Sisymbrietalia).
The life form of species proposed by Raunkiaer [52] was assigned according to the database “Ecological Flora of the British Isles” [53]. The following life forms were distinguished: phanerophytes, chamaephytes, hemicryptophytes, geophytes and therophytes. In the case of missing data the publication of Ellenberg et al. [54] was included.
The dispersal mode of species was assigned based on the database “Pladias” [55]. The following dispersal types were distinguished: Allium (mainly autochory, as well as anemochory, endozoochory, epizoochory), Bidens (mainly autochory and epizoochory, as well as endozoochory), Cornus (autochory and endozoochory), Epilobium (mainly anemochory and autochory, as well as endozoochory, epizoochory). The detailed description of dispersal modes can be found in the publication of Sádlo et al. [56].
The origin of species was assigned based on the database “Alien species in Poland” [57]. The alien species was understood as a species or lower taxon, introduced outside its natural past or present range that might survive and subsequently reproduce. The native species to a given area is a species that has been observed in the form of a naturally occurring and self-sustaining population from historical times.
Data concerning habitat affiliation and life form of Erigeron acris ssp. serotinus (Weihe) Greuter, which are lacking in the aforementioned sources, were taken from the publication of Pliszko [58]. Plants identified solely to the rank of a genus (e.g., Carex sp.) were excluded from the analyses. Moreover, the cultivated plants such as Cerasus vulgaris Mill. and Malus domestica Borkh. were excluded from the analysis of habitat affiliation.

2.5. The Data Analysis

The mean height of the tallest plant shoot, number of species, percentage of aboveground biomass damage by trampling, total plant cover percentage, as well as degree of cover-abundance of a particular species (±SD) were calculated in the research plots CL and FU, as well as in the plots located along narrow and wide pathways in each study site.
The normal distribution of the untransformed data was tested using the Kołmogorov-Smirnov test, whereas the homogeneity of variance was verified using the Levene test at the significance level of p < 0.05. The ANOVA analysis of main effects followed by the post-hoc Tukey HSD test was applied to check the statistical significance of the effect of pathway width and plot distance from the pathway on (i) the height of the tallest plant shoot, (ii) the number of species, (iii) total plant cover percentage, (iv) percentage of plant cover damaged by trampling, as well as (v) degree of cover-abundance of a particular species within the study plots. The aforementioned analyses were computed using a STATISTICA software (version 13). The chi-square test with Yates correction for continuity was applied to check whether there were significant differences among the plots located along the narrow and wide pathways, as well as in the plots situated at a diverse distance from the border of trails in cover-abundance degree of species showing various habitat affiliation, life form, seed dispersal mode and species origin. The chi-square test was conducted using the interactive calculation tool [59].

3. Results

3.1. The Plant Cover and Richness

The mean height of the tallest plant ranged from 66.2 cm to 123.7 cm (Figure A1) and it was similar in the plots situated along the narrow and wide pathways (F = 0.08, p = 0.77), at the same time it was significantly greater in the plots FU than in the plots CL (F = 31.64, p < 0.001). The mean number of species per plot amounted from 11.1 to 17.6 (Figure A1) and it did not differ in the plots situated along the narrow and wide pathways (F = 0.17, p = 0.67) but it was greater in the plots CL than FU (F = 5.39, p ≤ 0.05).The mean percentage of total plant cover achieved from 43.0 to 85.0 (Figure A2). The statistical analysis evidenced, that the values noted in the plots located along the narrow pathways were significantly lower than along the wide ones (F = 5.19, p ≤ 0.05) and they were similar in the plots CL and FU (F = 0.22, p = 0.63). The mean percentage of plant cover damaged by trampling achieved from 0.0 to 82.5 (Figure A2). It was similar in plots located along narrow and wide pathways (F = 0.01, p = 0.90) and remarkably greater in the plots CL than in the plots FU (F = 145.93, p < 0.001). The mean cover-abundance degree of particular species per plot according to the Braun-Blanquet scale ranged from 0.1 to 0.7 (Figure A3). The values recorded along the narrow pathways were greater than along the wide ones (F = 12.00, p < 0.001), whereas values noted in the plots CL and FU were similar (F = 0.15, p = 0.69).

3.2. The Species Groups Characteristics

Along the narrow and wide pathways, meadow and grassland species prevailed over ruderal plants, while forest taxa occurred sporadically. The statistical analysis showed a lack of differences in most study areas (Figure 2). The similar spectra of habitat affiliations were observed in the plots CL and FU in the majority of the study sites. Only in one study area, in closer plots, was the considerable dominance of ruderal taxa evidenced (Figure 3). The statistical analysis proved significant differences in life form spectra among the narrow and wide pathways (Figure 4), as well as among the plots CL and FU (Figure 5) regardless of the dominance of hemicryptophytes and chamaephytes, slight presence of phanerophytes and therophytes, as well as the lowest cover-abundance degree of geophytes in the majority of the study areas. The cover-abundance degrees of species with particular dispersal mode occurring in plots situated along pathways with different width varied significantly (Figure 6). In the majority of plots situated along the narrow pathways, the lowest cover-abundance degree showed species with dispersal type Bidens, while taxa with Allium, Cornus or Epilobium dispersal type prevailed in at least one study site. In the plots located along the wide pathways, different patterns of dispersal mode spectra were noticed. The statistical analysis showed that also the cover-abundance degrees of species with particular dispersal mode occurring in the plots CL and FU differed significantly (Figure 7). In most plots CL, species with Bidens type occurred sporadically, whereas in plots FU species with type Cornus dominated in the majority of places. Despite the prevalence of native species over alien species, the statistical analysis showed significant differences among the narrow and wide pathways (Figure 8), as well as among the plots CL and FU (Figure 9).

4. Discussion

4.1. The Plant Cover Characteristics

The performed observations evidenced that the values of height of the tallest plant shoots, species richness, as well as the percentage of plant cover damaged by trampling did not differ in the narrow and wide pathways. The height of the tallest plants achieves greater values in the distant plots than in the plots situated closely to the pathways, while species richness and percentage of plant cover damaged by trampling show an inversed trend. Therefore, our hypotheses that (i) the height of plants is lower in plots located near pathways than that in plots located away from pathways, (ii) the percentage of plant cover damaged by trampling is higher in plots located near pathways than that in plots located away from pathways, and (iv) the number of species is higher in plots located near pathways than that in plots located away from pathways can be fully accepted. At the same time, the hypothesis (iii) that the percentage of plant cover damaged by trampling is higher along narrow pathways than that along wide pathways must be rejected.
The lower height of the tallest plant in plots situated close to the tourist trails might be an effect of damage to plant tissue, especially shoot fractures by passers-by. Also, a much greater percentage of damaged plant cover by trampling in the close plots might be linked with the activity of visitors bypassing the pathways or descending from them due to the taking of photographs, curiosity, repose or other causes. Such tourist dispersion was frequently observed in trails by numerous authors e.g., [32,34].
The obtained results proving much greater species richness close to tourist trails correspond with the findings of Root-Bernstein and Svenning [60], while other investigators observed an inversed tendency [61]. A higher number of plant species near the tourist/recreation pathways within the calcareous grasslands can be explained by the fact that plant diaspores are easily transported on shoes, clothes and vehicles. Similarly, it was evidenced by Tikka et al. [62] that road verges serve as dispersal corridors for grassland species. It is also worth mentioning that some plants such as Lolium perenne L. and Trifolium repens L. tolerate trampling and often occur on roadside verges [23,63]. However, their abundance in the examined plots was rather low (except some plots with L. perenne). Moreover, tourist trails are often used for migration by wild animals (e.g., [64]), which may also promote the plant dispersal along the pathways.
The performed observations evidenced that the distance from the trails does not have an influence on total plant cover percentage, as well as the cover-abundance degree of a particular species per plot. The obtained results are not consistent with the studies of Jägerbrand and Alatalo [43], who noted that due to the decrease in understory cover, the abundance of litter, rock and soil increased with the proximity to the trail in alpine heath. The noted in the present studies lower values of total plant cover in the plots situated along the narrow pathways might indicate the occurrence of a greater number of gaps where bare substratum is visible. It is worth mentioning that such openings in continuous turf are considered as safe sites for seedling recruitment sensu Harper [65], regeneration niche sensu Grubb [66] and space “free from competition” [67]. The beneficial role of small-scale gaps enabling spontaneous recruitment and establishment of seedlings in calcareous grasslands was repeatedly proved in naturally originated [68], as well as experimentally made openings [69,70]. In the present study, the recorded greater mean cover-abundance degree of a species along the narrow pathways than along the wide ones might suggest the successful generative propagation and/or undisturbed vegetative spread, leading to the multiplication of individuals and/or ramet number, as well as an area of individuals presumably owing to the non-intensive use of trails by visitors. The increase of pathway width as the result of the augmentation of the intensity of tourist traffic, as well as the frequency of passes, was previously recorded among others by Kiszka [16].

4.2. The Species Groups Characteristics

Our study, showing that regardless of pathway width and distance from the trail, meadow and grassland species prevailed over ruderal plants, while forest taxa occurred sporadically, suggest that hypothesis (v) about the variability of habitat affiliation spectra must be rejected. Moreover, we evidenced the dominance of native species over alien species irrespective of pathway width and distance from the edge of the trail. Although the area of calcareous grasslands in Cracow has significantly decreased over the last decades [71], their semi-natural value is still high [72]. However, the presence of some alien species such as Erigeron annuus (L.) Desf., E. canadensis L., Robinia pseudoacacia L., Solidago canadensis L. and Vicia grandiflora Scop., which are invasive in Poland [73], suggests the negative effect of human activities on calcareous grasslands in the area of the city. These species can be easily introduced to calcareous grasslands from nearly located roadside verges, abandoned allotment gardens and waste ground. Nevertheless, it might be stated that despite the significant statistical differences regarding the presence of native and alien species along the narrow and wide pathways, as well as among the plots CL and FU, the dominance of native taxa suggests the rejection of hypothesis (v) about the variability of species origin spectra.
Also, in spite of recorded differences in the degree of cover-abundance of species representing particular life forms, depending on trail width and plot location, the similar patterns of life form spectra noticed in the majority of the study areas indicate the rejection of hypothesis (v) about the variability of species life form spectra. The performed investigations evidencing a dominance of hemicryptophytes and chamaephytes supports the findings of Dobay et al. [74], arguing that the species representing the aforementioned life forms are often found in grassland areas. Roovers et al. [38] observed the dominance of hemicryptophytes regardless of level recreational use in meadows, heaths, and forests, whilePescott and Stewart [75] added that vegetation dominated by hemicryptophytes recovers from trampling to a greater extent than vegetation dominated by other life forms. The observed in the present studies scarce number of phanerophytes is not remarkable considering the occurrence of forests in the vicinity of the study sites, whereas the slight abundance of therophytes seems to be very surprising and might be an effect of slight occurrence of diaspores in the soil seed bank and/or unsuitable conditions for seedling recruitment. Additionally, it is worth mentioning, that Skłodowski et al. [39], as well as Zdanowicz and Skłodkowski [40], found the greater number of therophytes along wide pathways than along narrow ones in forests. Apart from this, other researchers recorded a considerably greater share of therophytes in the borders of trails than in more distant sites in forests [37] and meadows [38].
According to Sádlo et al. [56], the dispersal strategies of Allium, Bidens, Cornus, Epilobium and Lycopodium are found within the plants occupying dry grasslands. In our study, we evidenced the presence of species with the strategies of Allium, Bidens, Cornus and Epilobium. The occurrence of different patterns of dispersal mode spectra among the plots located along the narrow and wide pathways, as well as among the plots CL and FU, allows confirming the hypothesis (v) about the variability of species dispersal mode spectra. Simultaneously, the results showing the lowest cover-abundance degree of species presenting Bidens dispersal type (mainly epizoochory and autochory, as well as endozoochory) in plots situated along narrow pathways, as well as in plots located close to the trail edge, might suggest low activity of tourist and visitors passing by pathways in the external transport of diaspores possessing mechanisms to adhere to clothes equipment, vehicles and animals. On the other hand, the prevalence of taxa with Cornus type (endozoochory and autochory) in plots located at a greater distance might be an effect of dung deposition by animals. The considerable recruitment of endozoochorous species seedlings from dung samples was observed in numerous habitats (e.g., [76,77,78]).

5. Conclusions

The height of the tallest plant shoots, species richness, as well as the percentage of plant cover damaged by trampling did not differ in the narrow and wide pathways. The significantly lower height of plants in close plots and the greater species number and percentage of plant cover damaged by trampling recorded there is the effect of passers-by contributing to the mechanical fracture of plant organs and the dissemination of diaspores. The distance from trails does not impact the total plant cover percentage, as well the cover-abundance degree of a particular species per plot. The lower value of plant cover percentage along narrow trails creates the opportunities for successful generative propagation and/or vegetative spread, resulting in a greater mean cover-abundance degree of a species.
The dominance of meadow and grassland species over ruderal plants and sporadic occurrence of forest taxa, as well as the prevalence of native species irrespective of pathway width and distance from trail edge, suggests that the composition of the examined patches of grasslands has not been drastically changed by secondary succession and human activity. The dominance of hemicryptophytes and chamaephytes, slight presence of phanerophytes and therophytes and the low cover-abundance degree of geophytes was observed in the majority of study areas regardless of path width and distance from the edge of the trail. The lowest cover-abundance degree of species presenting Bidens dispersal type in plots situated along narrow pathways, as well as in plots located close to the trail edge might suggest the low activity of visitors passing by pathways in the external transport of epizoochorous seeds. The prevalence of taxa with Cornus type in plots located at a greater distance might be an effect of deposition of dung containing endozoochorous seeds by animals.
The investigations performed enlarge the current state of knowledge about the properties of vegetation in the vicinity of visitor-created (informal) tourist trails in calcareous grasslands - areas of high conservation value. Our results can be applied in further studies to evaluate the temporal changes of species composition and plant traits, as well as for comparison with other popular semi-natural areas, where trampling is also an issue.
According to assumptions of plans of protection [79], to preserve the calcareous grasslands in the Natura 2000 areas, it is important to make awareness-raising efforts among the local population and tourists through educational campaigns. Moreover, the monitoring of frequently visited patches, enabling the identification of existing and potential threats caused by visitor activities, is desired.

Author Contributions

K.K.-G. conducted methodology of research and project administration, field research, data analysis, manuscript preparation and correction. A.P. conducted field research, data analysis, manuscript preparation and correction. K.G.-G. conducted field research, manuscript preparation and correction. All authors have read and agreed to the published version of the manuscript.

Funding

This research received funding from the University of Physical Education in Cracow as part of statutory research (project number 224/BS/KPiPPT/2019).

Conflicts of Interest

The authors declare no conflict of interest. The funder had no role in the design of the study, in the collection, analyses or interpretation of data, in the writing of the manuscript, or in the decision to publish the results.

Appendix A

Table
Table A1. The characteristics of species found in the plant cover of the studied calcareous grasslands regarding habitat affiliations according to Matuszkiewicz [61], life form according to Fitter and Peat [63], dispersal type according to Pladias [55]. Database of the Czech flora and vegetation [65], and origin according to Alien species in Poland [67].
Table A1. The characteristics of species found in the plant cover of the studied calcareous grasslands regarding habitat affiliations according to Matuszkiewicz [61], life form according to Fitter and Peat [63], dispersal type according to Pladias [55]. Database of the Czech flora and vegetation [65], and origin according to Alien species in Poland [67].
TaxonHabitatLife FormDispersal TypeOrigin
Acer platanoides L.ForestPhanerophyteEpilobiumNative
Acer pseudoplatanus L.ForestPhanerophyteEpilobiumNative
Achilleamillefolium L.MeadowChamaephyteAlliumNative
Acinosarvensis (Lam.) DandyGrasslandTherophyteAlliumNative
Aegopodium podagraria L.ForestHemicryptophyteAlliumNative
Agrimonia eupatoria L.GrasslandHemicryptophyteBidensNative
Agrostis capillaris L.GrasslandHemicryptophyteAlliumNative
Ajuga genevensis L.GrasslandHemicryptophyteAlliumNative
Allium montanum F. W. SchmidtGrasslandGeophyteAlliumNative
Alyssum alyssoides L.GrasslandTherophyteAlliumNative
Anchusa officinalis L.RuderalHemicryptophyteAlliumAlien
Anthyllis vulneraria L.GrasslandHemicryptophyteAlliumNative
Anthoxanthum odoratum L.MeadowHemicryptophyteAlliumNative
Arabidopsis thaliana (L.) Heynh.RuderalTherophyteAlliumNative
Arabis hirsuta (L.) Scop.GrasslandHemicryptophyteAlliumNative
Arenaria serpyllifolia L.GrasslandTherophyteAlliumNative
Arrhenatherum elatius (L.) P. Beauv. ex J. & C. PreslMeadowHemicryptophyteAlliumNative
Artemisia campestris L.GrasslandChamaephyteAlliumNative
Artemisia vulgaris L.RuderalHemicryptophyteAlliumNative
Asperula cynanchica L.GrasslandHemicryptophyteAlliumNative
Astragalus glycyphyllos L.GrasslandHemicryptophyteAlliumNative
Avenula pratensis (L.) Dumort.GrasslandHemicryptophyteAlliumNative
Avenula pubescens (Huds.) Dumort.MeadowHemicryptophyteAlliumNative
Briza media L.MeadowHemicryptophyteAlliumNative
Bromus erectus Huds.GrasslandHemicryptophyteAlliumNative
Bromus hordeaceus L.MeadowHemicryptophyteAlliumNative
Bromus sterilis L.RuderalTherophyteAlliumAlien
Calamagrostis epigejos (L.) Roth.RuderalHemicryptophyteEpilobiumNative
Calystegia sepium (L.) R. Br.RuderalHemicryptophyteAlliumNative
Carduus acanthoides L.RuderalHemicryptophyteEpilobiumAlien
Carex caryophyllea L.GrasslandHemicryptophyteAlliumNative
Carex hirta L.MeadowHemicryptophyteAlliumNative
Carex ovalis Gooden.GrasslandHemicryptophyteAlliumNative
Carex praecox Schreb.GrasslandHemicryptophyteAlliumNative
Carex sp.----
Carlina acaulis L.GrasslandHemicryptophyteEpilobiumNative
Centaurea stoebe TauschGrasslandHemicryptophyteAlliumNative
Cerastium arvense L.GrasslandChamaephyteAlliumNative
Cerasus sp.----
Cerasus vulgaris Mill.-PhanerophyteCornusAlien
Cerinthe minor L.RuderalHemicryptophyteAlliumNative
Cichorium intybus L.RuderalHemicryptophyteAlliumAlien
Convolvulus arvensis L.RuderalHemicryptophyteAlliumNative
Cornus sanguinea L.GrasslandPhanerophyteCornusNative
Coronilla varia L.GrasslandHemicryptophyteAlliumNative
Crataegus sp.----
Cuscuta epithymum L.GrasslandTherophyteAlliumNative
Dactylis glomerata L.MeadowHemicryptophyteAlliumNative
Daucus carota L.MeadowHemicryptophyteBidensNative
Deschampsia caespitosa (L.) P. B.MeadowHemicryptophyteAlliumNative
Dianthus carthusianorum L.GrasslandChamaephyteAlliumNative
Echium vulgare L.RuderalHemicryptophyteAlliumNative
Elymus hispidus (Opiz) MelderisRuderalHemicryptophyteAlliumNative
Elymus repens (L.) GouldRuderalHemicryptophyteAlliumNative
Erigeron acris ssp. serotinus (Weihe) GreuterGrasslandHemicryptophyteEpilobiumNative
Erigeron annuus (L.) Desf.RuderalHemicryptophyteEpilobiumAlien
Erigeron canadensis L.RuderalTherophyteEpilobiumAlien
Euonymus europaeus L.ForestPhanerophyteCornusNative
Euphorbia cyparissias L.GrasslandHemicryptophyteAlliumNative
Euphrasia stricta J. P. Wolff. ex LehmannGrasslandTherophyteAlliumNative
Fallopia convolvulus (L.) Á. LöveRuderalTherophyteAlliumAlien
Festuca pratensis Huds.MeadowHemicryptophyteAlliumNative
Festuca rubra L.MeadowHemicryptophyteAlliumNative
Festuca rupicola Heuff.GrasslandHemicryptophyteAlliumNative
Festuca sp.----
Fragaria viridis WestonGrasslandHemicryptophyteCornusNative
Galium mollugo L.MeadowHemicryptophyteAlliumNative
Galium verum L.GrasslandHemicryptophyteAlliumNative
Geranium pratense L.RuderalHemicryptophyteAlliumNative
Geum urbanum L.MeadowHemicryptophyteBidensNative
Helianthemum nummularium (L.) Mill.GrasslandChamaephyteAlliumNative
Hieracium pilosella L.GrasslandHemicryptophyteEpilobiumNative
Holcus lanatus L.MeadowHemicryptophyteAlliumNative
Hypericum perforatum L.RuderalHemicryptophyteAlliumNative
Knautia arvensis (L.) J. M. Coult.MeadowHemicryptophyteAlliumNative
Koeleria macrantha (Ledeb.) Schult.GrasslandHemicryptophyteAlliumNative
Leontodon autumnalis L.MeadowHemicryptophyteEpilobiumNative
Leontodon hispidus L.MeadowHemicryptophyteEpilobiumNative
Leucanthemum vulgare Lam.MeadowHemicryptophyteAlliumNative
Ligustrum vulgare L.GrasslandPhanerophyteCornusNative
Linaria vulgaris Mill.RuderalHemicryptophyteAlliumNative
Linum catharticum L.MeadowHemicryptophyteAlliumNative
Lolium perenne L.MeadowHemicryptophyteAlliumNative
Lotus corniculatus L.MeadowHemicryptophyteAlliumNative
Malus domestica Borkh.-PhanerophyteCornusAlien
Medicago falcata L.GrasslandHemicryptophyteAlliumNative
Medicago lupulina L.RuderalHemicryptophyteAlliumNative
Medicago sativa L.RuderalHemicryptophyteAlliumAlien
Pastinaca sativa L.MeadowHemicryptophyteAlliumAlien
Peucedanum oreoselinum (L.) MoenchGrasslandHemicryptophyteAlliumNative
Phleum phleoides (L.) H. Karst.GrasslandHemicryptophyteAlliumNative
Phleum pratense L.MeadowHemicryptophyteAlliumNative
Picris hieracioides L.RuderalHemicryptophyteEpilobiumNative
Pimpinella saxifraga L.MeadowHemicryptophyteAlliumNative
Plantago lanceolata L.GrasslandHemicryptophyteAlliumNative
Plantago major L.MeadowHemicryptophyteAlliumNative
Plantago media L.GrasslandHemicryptophyteAlliumNative
Poa compressa L.RuderalHemicryptophyteAlliumNative
Poa pratensis L.RuderalHemicryptophyteAlliumNative
Polygonum aviculare L.RuderalTherophyteAlliumNative
Populus tremula L.RuderalPhanerophyteEpilobiumNative
Potentilla arenaria Borkh.GrasslandHemicryptophyteAlliumNative
Potentilla argentea L.GrasslandHemicryptophyteAlliumNative
Potentilla reptans L.MeadowHemicryptophyteAlliumNative
Prunella vulgaris L.MeadowHemicryptophyteAlliumNative
Prunus sp.----
Prunus spinosa L.GrasslandPhanerophyteCornusNative
Rhamnus cathartica L.GrasslandPhanerophyteCornusNative
Ranunculus bulbosus L.GrasslandHemicryptophyteAlliumNative
Robinia pseudoacacia L.ForestPhanerophyteAlliumAlien
Rosa canina L.GrasslandPhanerophyteCornusNative
Rubus caesius L.GrasslandPhanerophyteCornusNative
Rumex crispus L.RuderalHemicryptophyteAlliumNative
Rumex obtusifolius L.RuderalHemicryptophyteAlliumNative
Rumex thyrsiflorus Fingerh.MeadowHemicryptophyteAlliumNative
Salvia pratensis L.GrasslandHemicryptophyteAlliumNative
Salvia verticillata L.GrasslandHemicryptophyteAlliumNative
Sanguisorba minor Scop.GrasslandHemicryptophyteAlliumNative
Sarothamnus scoparius(L.) Wimm.GrasslandPhanerophyteAlliumNative
Scabiosa ochroleuca L.GrasslandHemicryptophyteAlliumNative
Sedum acre L.GrasslandChamaephyteAlliumNative
Sedum sexangulare L.GrasslandChamaephyteAlliumNative
Senecio jacobaea L.RuderalHemicryptophyteEpilobiumNative
Seseli annuum L.GrasslandHemicryptophyteAlliumNative
Setaria viridis (L.) P. Beauv.RuderalTherophyteBidensAlien
Silene otites (L.) WibelGrasslandHemicryptophyteAlliumNative
Solidago canadensis L.RuderalHemicryptophyteEpilobiumAlien
Solidago gigantea AitonRuderalHemicryptophyteEpilobiumAlien
Solidago virgaurea L.GrasslandHemicryptophyteEpilobiumNative
Sonchus oleraceus L.RuderalHemicryptophyteEpilobiumAlien
Stachys recta L.GrasslandHemicryptophyteAlliumNative
Taraxacum sp.----
Thymus austriacus Bernh.GrasslandChamaephyteAlliumNative
Thymus glabrescens Willd.GrasslandChamaephyteAlliumNative
Thymus pulegioides L.GrasslandChamaephyteAlliumNative
Tragopogon pratensis L.MeadowHemicryptophyteEpilobiumNative
Trifolium arvense L.GrasslandTherophyteAlliumNative
Trifolium campestre Schreb.GrasslandTherophyteAlliumNative
Trifolium montanum L.MeadowHemicryptophyteAlliumNative
Trifolium pratense L.MeadowHemicryptophyteAlliumNative
Trifolium repens L.MeadowHemicryptophyteAlliumNative
Trisetum flavescens (L.) P. Beauv.GrasslandHemicryptophyteAlliumNative
Verbascum lychnitis L.GrasslandHemicryptophyteAlliumNative
Verbascum thapsus L.RuderalHemicryptophyteAlliumNative
Veronica arvensis L.RuderalTherophyteAlliumAlien
Veronica austriaca L.GrasslandChamaephyteAlliumNative
Veronica chamaedrys L.RuderalChamaephyteAlliumNative
Veronica spicata L.GrasslandChamaephyteAlliumNative
Vicia cracca L.MeadowHemicryptophyteAlliumNative
Vicia grandiflora Scop.RuderalTherophyteAlliumAlien
Vicia hirsuta (L.) S. F. GrayRuderalTherophyteAlliumAlien
Vicia tetrasperma (L.) Schreb.RuderalTherophyteAlliumAlien
Vincetoxicum hirundinaria Medik.GrasslandHemicryptophyteEpilobiumNative
Viola hirta L.GrasslandHemicryptophyteAlliumNative
Viola odorata L.RuderalHemicryptophyteAlliumNative
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Figure A1. The mean height (cm) of the tallest plant (± SD) and number of species (± SD) in the closer (CL) and further (FU) plots located along the narrow-N (width ≤ 50 cm) and wide-W (width ≥ 115 cm) pathways situated within the investigated study sites.
Figure A1. The mean height (cm) of the tallest plant (± SD) and number of species (± SD) in the closer (CL) and further (FU) plots located along the narrow-N (width ≤ 50 cm) and wide-W (width ≥ 115 cm) pathways situated within the investigated study sites.
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Figure A2. The mean percentage of total plant cover (± SD) and the percentage of plant cover damaged by trampling (± SD) in the closer (CL) and further (FU) plots located along the narrow-N (width ≤ 50 cm) and wide-W (width ≥ 115 cm) pathways situated within the investigated study sites.
Figure A2. The mean percentage of total plant cover (± SD) and the percentage of plant cover damaged by trampling (± SD) in the closer (CL) and further (FU) plots located along the narrow-N (width ≤ 50 cm) and wide-W (width ≥ 115 cm) pathways situated within the investigated study sites.
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Figure A3. The mean cover-abundance degree of a particular species according to the Braun-Blanquet scale (± SD) in the closer (CL) and further (FU) plots located along the narrow-N (width ≤ 50 cm) and wide-W (width ≥ 115 cm) pathways situated within the investigated study sites.
Figure A3. The mean cover-abundance degree of a particular species according to the Braun-Blanquet scale (± SD) in the closer (CL) and further (FU) plots located along the narrow-N (width ≤ 50 cm) and wide-W (width ≥ 115 cm) pathways situated within the investigated study sites.
Sustainability 12 00454 g0a3

References

  1. Kruczek, Z. Tourists vs. Residents. The Influence of Excessive Tourist Attendance on the Process of Gentrification of Historic Cities on the Example of Kraków. Tur. Kult. 2018, 3, 21–49. [Google Scholar]
  2. Martín Martín, J.M.; GuaitaMartínez, J.M.; SalinasFernández, J.A. An Analysis of the Factors behind the Citizen’s Attitude of Rejection towards Tourism in a Context of Overtourism and Economic Dependence on This Activity. Sustainability 2018, 10, 2851. [Google Scholar] [CrossRef] [Green Version]
  3. Hospers, G.-J. Overtourism in Euro pean cities: From challenges to coping strategies. CESifo Forum 2019, 20, 20–24. [Google Scholar]
  4. Milano, C.; Novelli, M.; Cheer, J.M. Overtourism and degrowth: A social movements perspective. J. Sustain. Tour. 2019, 27, 1857–1875. [Google Scholar] [CrossRef]
  5. Capocchi, A.; Vallone, C.; Pierotti, M.; Amaduzzi, A. Overtourism: A Literature Review to Assess Implications and Future Perspectives. Sustainability 2019, 11, 3303. [Google Scholar] [CrossRef] [Green Version]
  6. Koens, K.; Postma, A.; Papp, B. Isovertourism overused? Understanding the impact of tourism in a city context. Sustainability 2018, 10, 4384. [Google Scholar] [CrossRef] [Green Version]
  7. Kruczek, Z. Overtourism”-aroundthedefinition. Encyclopedia 2019, 1. Available online: https://encyclopedia.pub/163 (accessed on 6 December 2019).
  8. Witkowski, Z. Wpływ turystyki na ochronę przyrody. In Integralna Ochrona Przyrody; Grzegorczyk, M., Ed.; Institute of Nature Conservation PAS: Kraków, Poland, 2007; pp. 187–189. [Google Scholar]
  9. Witkowski, Z.; Adamski, P.; Mroczka, A.; Ciapała, S. Limits of tourism and recreation interference in land areas of national parks and nature reserves. Prądnik 2010, 20, 427–440. [Google Scholar]
  10. Partyka, J. Tourist traffic in Polish national parks. Folia Tur. 2010, 22, 9–23. [Google Scholar]
  11. Fidelus, J.; Rogowski, M. Geomorphological effects of tourist usage of the mountain ridges on the example oftourist footpaths in the Western Tatra Mountains (Poland) and the Bucegi Mountains (Romania). Landf. Anal. 2012, 19, 29–40. [Google Scholar]
  12. Duda, T. Zrównoważona turystyka kulturowa na obszarach przyrodniczo cennych. Studium przypadku Drawieńskiego Parku Narodowego. Tur. Kult. 2018, 7, 102–108. [Google Scholar]
  13. Kapera, I. Sustainable Development of Tourism. Environmental, Social, and Economic Issues on the Example of Poland, 1st ed.; Andrzej Frycz Modrzewski Krakow University: Kraków, Poland, 2018; pp. 87–102. [Google Scholar]
  14. Kruczek, Z. Tourist traffic in national parks and consequences of excessive frequency of visitors. In National Parks and Socio-Economic Environment. Condemned to Dialogue, 1st ed.; Nocoń, M., Pasierbek, T., Sobczuk, J., Walas, B., Eds.; The University College of Tourism and Ecology: Sucha Beskidzka, Poland, 2019; pp. 160–177. [Google Scholar]
  15. Balmford, A.; Green, J.M.H.; Anderson, M.; Beresford, J.; Huang, C.; Naidoo, R.; Walpole, M.; Manica, A. Walk on the wild side: Estimating the global magnitude of visits to protected areas. PLoS Biol. 2015, 13, 1002074. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  16. Kiszka, K. Degradation of tourist routes in the Pieniny Mts. caused by hiking. Pienin—Przyr. Człowiek 2016, 14, 145–165. [Google Scholar]
  17. Leung, Y.-F.; Marion, J.L. Recreation impacts and management in wilderness: A state-of-knowledge review. In Proceedings of the Wilderness Science in a Time of Change Conference—Vol. 5, Wilderness Ecosystems, Threats, and Management, Missoula, MT, USA, 23–27 May 1999; Cole, D.N., McCool, S.F., Borrie, W.T., O’Loughlin, J., Eds.; Department of Agriculture, Forest Service, Rocky Mountain Research Station: Fort Collins, CO, USA, 1999; pp. 23–48. [Google Scholar]
  18. Kołodziejczyk, K. Standards for Infrastructure on Tourist Trails Based on Selected European Examples, 1st ed.; Institute of Geography and Regional Development: Wrocław, Poland, 2015; 459p. [Google Scholar]
  19. Kuss, F.R.; Graefe, A.R. Effects of recreation trampling on natural area vegetation. J. Leis. Res. 1985, 17, 165–183. [Google Scholar] [CrossRef]
  20. Wichmann, M.C.; Alexander, M.J.; Soons, M.B.; Galsworthy, S.; Dunne, L.; Gould, R.; Fairfax, Ch.; Niggemann, M.; Hails, R.S.; Bullock, J.M. Human-mediated dispersal of seeds over long distances. Proc. R. Soc. B Biol. Sci. 2008, 276, 523–532. [Google Scholar] [CrossRef] [Green Version]
  21. Pickering, C.; Mount, A. Do tourists disperse weed seed? A global review of unintentional human-mediated terrestrial seed dispersal on clothing, vehicles and horses. J. Sustain. Tour. 2010, 18, 239–256. [Google Scholar] [CrossRef]
  22. Anderson, L.G.; Rocliffe, S.; Haddaway, N.R.; Dunn, A.M. The role of tourism and recreation in the spread of non-native species: A systematic review and meta-analysis. PLoS ONE 2015, 10, e0140833. [Google Scholar] [CrossRef]
  23. Sun, D.; Liddle, M.J. Plant morphological characteristics and resistance tosimulated trampling. Environ. Manag. 1993, 17, 511–521. [Google Scholar] [CrossRef]
  24. Kissling, M.; Hegetschweiler, K.T.; Rusterholz, H.P.; Baur, B. Short-term and long-term effects of human trampling on above-ground vegetation, soildensity, soilorganic matter and soil microbial processes in suburban beech forests. Appl. Soil Ecol. 2009, 42, 303–314. [Google Scholar] [CrossRef]
  25. Pickering, C.M.; Growcock, A.J. Impacts of experimental trampling on tall alpine herb fields and subalpine grasslands in the Australian Alps. J. Environ. Manag. 2009, 91, 532–540. [Google Scholar] [CrossRef]
  26. Dumitraşcu, M.; Marin, A.; Preda, E.; Ţîbîrnac, M.; Vădineanu, A. Tramplingeffectsonplantspeciesmorphology. Rom. J. Biol.- Plant Biol. 2010, 55, 89–96. [Google Scholar]
  27. Bernhardt-Römermann, M.; Gray, A.; Vanbergen, A.J.; Bergès, L.; Bohner, A.; Brooker, R.W.; DeBruyn, L.; DeCinti, B.; Dirnböck, T.; Grandin, U.; et al. Functional traits and local environment predict vegetation responses to disturbance: A pan-European multi-site experiment. J. Ecol. 2011, 99, 777–787. [Google Scholar] [CrossRef]
  28. Korkanç, S.Y. Impacts of recreational human trampling on selected soil and vegetation properties of Aladag Natural Park, Turkey. Catena 2014, 113, 219–225. [Google Scholar] [CrossRef]
  29. Mason, S.; Newsome, D.; Moore, S.; Admiraal, S. Recreational trampling negatively impacts vegetation structure of an Australian biodiversity hot spot. Biodivers Conserv. 2015, 24, 2685–2707. [Google Scholar] [CrossRef] [Green Version]
  30. Runnström, M.C.; Ólafsdóttir, R.; Blanke, J.; Berlin, B. Image analysis to monitor experimental trampling and vegetation recovery in Icelandic plant communities. Environments 2019, 6, 99. [Google Scholar] [CrossRef] [Green Version]
  31. Grabherr, G. The impact of trampling by tourists on a high altitudinal grasslandin the Tyrolean Alps, Austria. Vegetatio 1982, 48, 209–219. [Google Scholar]
  32. Gmyrek-Gołąb, K.; Krauz, K.; Łabaj, M.; Mroczka, A.; Tadel, A.; Witkowski, Z. Tourist dispersion around a trail in ‘WawozHomole’[HomoleGeorge] naturereserve. Nat. Conserv. 2005, 61, 61–64. [Google Scholar]
  33. Wenjun, L.; Xiaodong, G.; Chunyan, L. Hiking trail sand tourism impact assessment in protected area: Jiuzhaigou Biosphere Reserve, China. Environ. Monit. Assess. 2005, 108, 279–293. [Google Scholar]
  34. Kolasińska, A.; Adamski, P.; Ciapała, S.; Švajda, J.; Witkowski, Z. Trail management, off-trail walking and visitor impact in the Pieniny Mts National Park (PolishCarpathians). Eco-Mont 2015, 7, 26–36. [Google Scholar]
  35. Dale, D.; Weaver, T. Trampling effects on vegetation of the trail corridors of North Rocky Mountain Forests. J. Appl. Ecol. 1974, 11, 767–772. [Google Scholar] [CrossRef]
  36. Bright, J.A. Hiker impact on herbaceous vegetation along trails in an evergreen woodland of Central Texas. Biol. Conserv. 1986, 36, 53–69. [Google Scholar] [CrossRef]
  37. Hall, C.N.; Kuss, F.R. Vegetation alternation along trials in Shenandoah National Park, Virginia. Biol. Conserv. 1989, 48, 211–227. [Google Scholar] [CrossRef]
  38. Roovers, P.; Verheyen, K.; Hermy, M.; Gulinck, H. Experimental trampling and vegetation recovery in some forest and heathland communities. Appl. Veg. Sci. 2004, 7, 111–118. [Google Scholar] [CrossRef]
  39. Skłodowski, J.W.; Bartosz, S.; Dul, Ł.; Grzybek, D.; Jankowski, S.; Kajetanem, M.; Kalisz, P.; Korenkiewicz, U.; Mazur, G.; Myszek, J.; et al. An attempt to assess the effect of tourist trail width on adjacen tforest environment. Sylwan 2009, 153, 699–709. [Google Scholar]
  40. Zdanowicz, E.; Skłodkowski, S. Evaluation of changes in environment around recreational routes on the example of Bielański Forest Reserve in Warsaw. Studia I Mater. CEPL W Rogowie 2013, 37, 348–355. [Google Scholar]
  41. Atik, M.; Sayan, S.; Karaguzel, O. Impact of recreational trampling on the natural vegetation in Termessos National Park, Antalya-Turkey. Tarim Bilimleri Dergisi 2009, 15, 249–258. [Google Scholar]
  42. Gremmen, N.J.M.; Smith, V.R.; vanTongeren, O.F.R. Impact of trampling on the vegetation of subantarctic Marion Island. Arc. Antarc. Alp. Res. 2003, 35, 442–446. [Google Scholar] [CrossRef] [Green Version]
  43. Jägerbrand, A.K.; Alatalo, J.M. Effects of human trampling on abundance and diversity of vascular plants, bryophytes and lichens in alpine heath vegetation, Northern Sweden. Springerplus 2015, 4, 1–12. [Google Scholar] [CrossRef] [Green Version]
  44. Kutiel, P.; Zhevelev, H.; Harrison, R. The effect of recreational impacts on soil and vegetation of stabilised coastal dunes in the Sharon Park, Israel. Ocean Coast. Manag. 1999, 42, 1041–1060. [Google Scholar] [CrossRef]
  45. Interpretation Manual of European Union Habitats-Eur 27. Available online: http://ec.europa.eu/environment/nature/legislation/habitatsdirective/docs/2007_07_im.pdf (assessed on 7 December 2019).
  46. Matuszko, D.; Piotrowicz, K. Characteristics of urban climate and the climate of Krakow. In The City in the Study of Geographers, 1st ed.; Trzepacz, P., Więcław-Michniewska, J., Brzosko-Sermak, A., Kołos, A., Eds.; Institute of Geography and Spatial Management, Jagiellonian University: Kraków, Poland, 2015; pp. 221–241. [Google Scholar]
  47. Perzanowska, J. Podgórki Tynieckie. In Treasures of Nature and Culture of Krakow and the Surrounding Area. Ecological Educational Paths; Grzegorczyk, M., Perzanowska, J., Eds.; Institute of Nature Conservation PAS and, WAM: Kraków, Poland, 2005; pp. 307–341. [Google Scholar]
  48. Csapodý, V. Keimlingsbestimmungs-Buch der Dikotyledonen; Akademiai Kiado: Budapeszt, Hungary, 1968; 286p. [Google Scholar]
  49. Muller, F.M. Seedlings of the North-Western European Lowland. A Flora of Seedlings, 1st ed.; Junk, B.V., Ed.; Springer Netherlands: Haarlem, The Netherlands, 1978; 653p. [Google Scholar]
  50. Braun-Blanquet, J. Pflanzensoziologie, Grundzüge der Vegetationskunde, 3rd ed.; Springer: Berlin, Germany, 1964; 631p. [Google Scholar]
  51. Matuszkiewicz, W.A. Guide for Identification of Polish Plant Communities; Polish Scientific Publishers PWN: Warsaw, Poland, 2017; 536p. [Google Scholar]
  52. Raunkiaer, C. The Life Forms of Plants and Statistical Plant Geography; Oxford University Press: London, UK, 1934; 632p. [Google Scholar]
  53. Fitter, A.H.; Peat, H.J. The Ecological Flora Database. J. Ecol. 1994, 82, 415–425. Available online: http://www.ecoflora.co.uk (assessed on 7 December 2019). [CrossRef]
  54. Ellenberg, H.; Weber, H.E.; Düll, R.; Wirth, V.; Werner, W.; Paulißen, D. Zeigerwerte von Pflanzen in Mitteleuropa. ScriptaGeobot. 1992, 18, 3–258. [Google Scholar]
  55. Pladias. Database of the Czech Flora and Vegetation. 2014–2019. Available online: http://www.pladias.org (assessed on 7 December 2019).
  56. Sádlo, J.; Chytrý, M.; Pergl, J.; Pyšek, P. Plant dispersal strategies: A new classification based on the multiple dispersal modes of individuals pecies. Preslia 2018, 90, 1–22. [Google Scholar] [CrossRef] [Green Version]
  57. Alien Species in Poland. 2009. Available online: http://www.iop.krakow.pl/ias/species (assessed on 7 December 2019).
  58. Pliszko, A. Additional data to the occurrence of Erigeron acris subsp. Serotinus (Weihe) Greuter (Asteraceae) in Europe. Steciana 2014, 18, 29–31. [Google Scholar]
  59. Calculation for the Chi-Square Test: An Interactive Calculation Tool for Chi-Square Tests of Goodness of Fit and Independence. 2001. Available online: http://quantpsy.org (assessed on 7 December 2019).
  60. Root-Bernstein, M.; Svenning, J.C. Human paths have positive impacts on plant richness and diversity: Ameta-analysis. Ecol. Evol. 2018, 8, 11111–11121. [Google Scholar] [CrossRef] [PubMed]
  61. Ballantyne, M.; Pickering, C.M.; McDougall, K.L.; Wright, G.T. Sustained impacts of a hiking trail on changing Windswept Feldmark vegetation in the Australian Alps. Aust. J. Bot. 2014, 62, 263–275. [Google Scholar] [CrossRef] [Green Version]
  62. Tikka, P.M.; Högmander, H.; Koski, P.S. Road and railway verges serve as dispersal corridors for grasslandplants. Landsc. Ecol. 2001, 16, 659–666. [Google Scholar] [CrossRef]
  63. Sun, D. Trampling resistance, recovery and growth rate of eight plant species. Agric. Ecosyst. Environ. 1992, 38, 165–273. [Google Scholar] [CrossRef]
  64. Snetsinger, S.D.; White, K. Recreation and Trail Impacts on Wildlife Species of Interest in Mount Spokane State Park; Pacific Biodiversity Institute, Winthrop: Washington, DC, USA, 2009; 60p. [Google Scholar]
  65. Harper, J.L. The Population Biology of Plants, 1st ed.; Academic Press: London, UK, 1977; 892p. [Google Scholar]
  66. Grubb, P.J. The maintenance of species-richness in plant communities: The importance of the regeneration niche. Biol. Rev. 1977, 52, 107–145. [Google Scholar] [CrossRef]
  67. Bullock, J.M. Gaps and seedling colonization. In Seeds: The Ecology of Regeneration in Plant Communities, 2nd ed.; Fenner, M., Ed.; CABI Publishing: NewYork, NY, USA, 2000; pp. 375–395. [Google Scholar]
  68. Kalamees, R.; Zobel, M. The role of the seed bank in gap regeneration in a calcareous grassland community. Ecology 2002, 83, 1017–1025. [Google Scholar] [CrossRef]
  69. Bullock, J.M.; Hill, B.C.; Silvertown, J.; Sutton, M. An experimental study of the effects of sheep grazing on vegetation change in a species-poor grasslands and the role of seedling recruitment intogaps. J. Appl. Ecol. 1994, 31, 493–507. [Google Scholar] [CrossRef]
  70. Bąba, W.; Kompała-Bąba, A. Do small-scale gaps in calcareous grassland swards facilitates eedling establishment? Acta Soc. Bot. Pol. 2005, 74, 125–131. [Google Scholar] [CrossRef] [Green Version]
  71. Heise, W. The Impact of Landscape Structure and Use History on the Flora and Vegetation of Calcareous Grasslands in Krakow. Ph.D. Thesis, Institute of Botany, Jagiellonian University, Kraków, Poland, 2014. [Google Scholar]
  72. Mydłowski, M. (Ed.) Directions of Development and Management of Green Areas in Krakow for 2017–2030. Anex II: Nature Conservation; Department of Environmental Management: Krakow, Poland, 2016; 256p. [Google Scholar]
  73. Tokarska-Guzik, B.; Dajdok, Z.; Zając, M.; Zając, A.; Urbisz, A.; Danielewicz, W.; Hołdyński, C. Alien Plants in Poland with Particular Reference to Invasive Species; General Directorate for Environmental Protection: Warsaw, Poland, 2012; 197p. [Google Scholar]
  74. Dobay, G.; Dobay, B.; Falusi, E.; Hajnáczki, S.; Penksza, K.; Bajor, Z.; Lampert, R.; Bakó, G.; Wichmann, B.; Szerdahelyi, T. Effects of sport tourism on temperate grasslandcommunities (Duna-IpolyNationalPark, Hungary). Appl. Ecol. Environ. Res. 2017, 15, 457–472. [Google Scholar] [CrossRef]
  75. Pescott, O.L.; Stewart, G.B. Assessing the impact of human trampling on vegetation: A systematic review and meta-analysis of experimental evidence. Peer J. 2014, 2, e360. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  76. Malo, J.E.; Jiménez, B.; Suárez, F. Herbivore dunging and endozoochorous seed deposition in a Mediterranean dehesa. J. Rangel. Manag. 2000, 53, 322–328. [Google Scholar] [CrossRef]
  77. Cosyns, E.; Claerbout, S.; Lamoot, I.; Hoffmann, M. Endozoochorous seed dispersal by cattle and horse in as patially heterogeneous landscape. Plant Ecol. 2005, 178, 149–162. [Google Scholar] [CrossRef]
  78. Kuiters, A.T.; Huiskes, H.P.J. Potential of endozoochorous seed dispersal by sheep in calcareous grasslands: Correlations with seed traits. Appl. Veg. Sci. 2010, 13, 163–172. [Google Scholar] [CrossRef]
  79. Protection Plans for Natura 2000 Areas. Available online: http://krakow.rdos.gov.pl/plany-zadan-ochronnych (assessed on 2 January 2020).
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Figure 1. The localisation of the study sites (A) and the plot sampling design (B). Abbreviations of study sites:B—Bogucianka, FB – Fort Bodzów, GP—Górka Pychowicka, T—Tyniec, UK—Uroczysko Kowadza, UW—Uroczysko Wielkanoc; Z—Zakrzówek; abbreviations of plots: CL—located close to the edge of tourist trail, FU—located away from the tourist trail.
Figure 1. The localisation of the study sites (A) and the plot sampling design (B). Abbreviations of study sites:B—Bogucianka, FB – Fort Bodzów, GP—Górka Pychowicka, T—Tyniec, UK—Uroczysko Kowadza, UW—Uroczysko Wielkanoc; Z—Zakrzówek; abbreviations of plots: CL—located close to the edge of tourist trail, FU—located away from the tourist trail.
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Figure 2. The mean cover-abundance degree of a species (± SD) affiliated to the forest (F), meadow (M), grassland (G), and ruderal habitats (R) per plot located along the narrow-N (width ≤ 50 cm) and wide-W (width ≥ 115 cm) pathways situated within the investigated study sites. The statistical significance level of χ2 test (df = 3): ns – not significant, * p ≤ 0.05, ** p < 0.01, *** p < 0.001.
Figure 2. The mean cover-abundance degree of a species (± SD) affiliated to the forest (F), meadow (M), grassland (G), and ruderal habitats (R) per plot located along the narrow-N (width ≤ 50 cm) and wide-W (width ≥ 115 cm) pathways situated within the investigated study sites. The statistical significance level of χ2 test (df = 3): ns – not significant, * p ≤ 0.05, ** p < 0.01, *** p < 0.001.
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Figure 3. The mean cover-abundance degree of a species (± SD) affiliated to forest (F), meadow (M), grassland (G), and ruderal habitats (R) per closer (CL) and further (FU) plot within the investigated study sites. The statistical significance level of χ2 test (df = 3) is given in Figure 2.
Figure 3. The mean cover-abundance degree of a species (± SD) affiliated to forest (F), meadow (M), grassland (G), and ruderal habitats (R) per closer (CL) and further (FU) plot within the investigated study sites. The statistical significance level of χ2 test (df = 3) is given in Figure 2.
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Figure 4. The mean cover-abundance degree of a species (± SD) representing phanerophytes (PH), chamaephytes (CH), hemicryptophytes (H), geophytes (G) and therophytes (T) per plot located along the narrow-N (width ≤ 50 cm) and wide-W (width ≥ 115 cm) pathways within the investigated study sites. The statistical significance level of χ2 test (df = 4) is given in Figure 2.
Figure 4. The mean cover-abundance degree of a species (± SD) representing phanerophytes (PH), chamaephytes (CH), hemicryptophytes (H), geophytes (G) and therophytes (T) per plot located along the narrow-N (width ≤ 50 cm) and wide-W (width ≥ 115 cm) pathways within the investigated study sites. The statistical significance level of χ2 test (df = 4) is given in Figure 2.
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Figure 5. The mean cover-abundance degree of a species (± SD) representing phanerophytes (PH), chamaephytes (CH), hemicryptophytes (H), geophytes (G) and therophytes (T) per closer (CL) and further (FU) plot within the investigated study sites. The statistical significance level of χ2 test (df = 4) is given in Figure 2.
Figure 5. The mean cover-abundance degree of a species (± SD) representing phanerophytes (PH), chamaephytes (CH), hemicryptophytes (H), geophytes (G) and therophytes (T) per closer (CL) and further (FU) plot within the investigated study sites. The statistical significance level of χ2 test (df = 4) is given in Figure 2.
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Figure 6. The mean presence of a species (± SD) representing dispersal mode Allium (A), Bidens (B), Cornus (C) and Epilobium (E) per plot located along narrow-N (width ≤ 50 cm) and wide-W (width ≥ 115 cm) pathways situated within the investigated study sites. The statistical significance level of χ2 test (df = 3) is given in Figure 2.
Figure 6. The mean presence of a species (± SD) representing dispersal mode Allium (A), Bidens (B), Cornus (C) and Epilobium (E) per plot located along narrow-N (width ≤ 50 cm) and wide-W (width ≥ 115 cm) pathways situated within the investigated study sites. The statistical significance level of χ2 test (df = 3) is given in Figure 2.
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Figure 7. The mean presence of a species (±SD) representing dispersal mode Allium (A), Bidens (B), Cornus (C) and Epilobium (E) per closer (CL) and further (FU) plot within investigated study sites. The statistical significance level of χ2 test (df = 3) is given in Figure 2.
Figure 7. The mean presence of a species (±SD) representing dispersal mode Allium (A), Bidens (B), Cornus (C) and Epilobium (E) per closer (CL) and further (FU) plot within investigated study sites. The statistical significance level of χ2 test (df = 3) is given in Figure 2.
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Figure 8. The mean cover-abundance degree of alien (A) and native (N) species (± SD) per plot located along the narrow-N (width ≤ 50 cm) and wide-W (width ≥ 115 cm) pathways within the investigated study sites. The statistical significance level of χ2 test (df = 1) is given in Figure 2.
Figure 8. The mean cover-abundance degree of alien (A) and native (N) species (± SD) per plot located along the narrow-N (width ≤ 50 cm) and wide-W (width ≥ 115 cm) pathways within the investigated study sites. The statistical significance level of χ2 test (df = 1) is given in Figure 2.
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Figure 9. The mean cover-abundance degree of alien (A) and native (N) species (± SD) per closer (CL) and further (FU) plot within the investigated study sites. The statistical significance level of χ2 test (df = 1) is given in Figure 2.
Figure 9. The mean cover-abundance degree of alien (A) and native (N) species (± SD) per closer (CL) and further (FU) plot within the investigated study sites. The statistical significance level of χ2 test (df = 1) is given in Figure 2.
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Table
Table 1. The Characteristics of Study Sites.
Table 1. The Characteristics of Study Sites.
Study SiteTourist/Recreation InfrastructureWidth of Pathway (cm)Coordinates and Elevation of Pathway
within the Study Areain the Vicinity of the Study AreaNarrowWideNarrowWide
BoguciankaVantage point, information boardFootball stadium4615050°00.555’50°00.675’
N/19°48.909’;N/19°48.914’;
244 m a.s.l. 1251 m a.s.l.
Fort BodzówVantage points, benches, bins, shelters, motor sports pathsRope park5024050°02.031’50°01.978’
N/19°52.576’; N/19°51.891’;
250 m a.s.l.238 m a.s.l.
Górka PychowickaVantage points, benches, bins, shelters, fire circles, information boardMotor sports paths, bike paths5018050°01.823’50°01.850’
N/19°52.996’; N/19°52.996’;
225 m a.s.l.225 m a.s.l.
TyniecVantage point, motor sports paths,-3633550°00.301’50°00.313’
N/19°49.095’; N/19°49.125’;
256 m a.s.l.254 m a.s.l.
Uroczysko KowadzaVantage point, benches-3513150°00.884’50°00.880’
N/19°46.638’; N/19°49.648’;
268 m a.s.l.266 m a.s.l.
UroczyskoWielkanocVantage point, benches, bins, information board-3011550°00.959’50°00.938’
N/19°48.850’; N/19°48.840’;
264 m a.s.l.260 m a.s.l.
ZakrzówekVantage points, climbing walls, information boardLagoon created inthe lime quarry, bike paths3312050°02.365’50°02.415’
N/19°54.987’; N/19°54.752’;
203 m a.s.l.213 m a.s.l.
1 above sea level.
Table
Table 2. The mean light intensity (Lx) (± SD), soil moisture (± SD) and soil pH (± SD) noted in closer (CL) and further (FU) plots located along the narrow (width ≤ 50 cm) and wide (width ≥ 115 cm) pathways situated within the investigated study site.
Table 2. The mean light intensity (Lx) (± SD), soil moisture (± SD) and soil pH (± SD) noted in closer (CL) and further (FU) plots located along the narrow (width ≤ 50 cm) and wide (width ≥ 115 cm) pathways situated within the investigated study site.
Study Sites
Górka PychowickaFort BodzówBoguciankaUroczysko WielkanocZakrzówekUroczysko KowadzaTyniec
Light intensityNarrowCL200011502000200017202000740
(±0.0)(±400.6)(±0.0)(±0.0)(±489.4)(±0.0)(±508.1)
FU200010202000200016902000690
(±0.0)(±498.4)(±0.0)(±0.0)(±499.8)(±0.0)(±499.8)
WideCL1820185020001950146020001090
(±423.73)(±337.4)(±0.0)(±158.1)(±614.9)(±0.0)(±502.1)
FU168016802000180012701900830
(±474.6)(±518.1)(±0.0)(±421.6)(±551.8)(±316.2)(±447.3)
Soil moistureNarrowCL2.511.36.743.74.5
(±0.6)(±0.0)(±0.3)(±2.1)(±1.0)(±2.3)(±2.2)
FU1.711.24.33.63.54.6
(±0.8)(±0.0)(±0.3)(±2.3)(±1.1)(±1.5)(±2.2)
WideCL111.25.84.93.75.5
(±0.0)(±0.0)(±0.2)(±1.9)(±1.6)(±1.8)(±1.8)
FU111.15.43.934.4
(±0.0)(±0.0)(±0.2)(±1.8)(±1.1)(±0.7)(±1.7)
Soil pHNarrowCL7.47.57.57.37.37.47.2
(±0.2)(±0.0)(±0.0)(±0.4)(±0.3)(±0.2)(±0.3)
FU7.57.57.57.47.47.27.1
(±0.2)(±0.0)(±0.0)(±0.2)(±0.2)(±0.3)(±0.2)
WideCL7.87.57.57.37.47.27.3
(±0.3)(±0.2)(±0.0)(±0.3)(±0.2)(±0.3)(±0.3)
FU7.77.57.57.57.47.47.4
(±0.3)(±0.0)(±0.0)(±0.2)(±0.3)(±0.2)(±0.2)

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Kostrakiewicz-Gierałt, K.; Pliszko, A.; Gmyrek-Gołąb, K. The Effect of Visitors on the Properties of Vegetation of Calcareous Grasslands in the Context of Width and Distances from Tourist Trails. Sustainability 2020, 12, 454. https://doi.org/10.3390/su12020454

AMA Style

Kostrakiewicz-Gierałt K, Pliszko A, Gmyrek-Gołąb K. The Effect of Visitors on the Properties of Vegetation of Calcareous Grasslands in the Context of Width and Distances from Tourist Trails. Sustainability. 2020; 12(2):454. https://doi.org/10.3390/su12020454

Chicago/Turabian Style

Kostrakiewicz-Gierałt, Kinga, Artur Pliszko, and Katarzyna Gmyrek-Gołąb. 2020. "The Effect of Visitors on the Properties of Vegetation of Calcareous Grasslands in the Context of Width and Distances from Tourist Trails" Sustainability 12, no. 2: 454. https://doi.org/10.3390/su12020454

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