Next Article in Journal
Bark Features for Identifying Resonance Spruce Standing Timber
Previous Article in Journal
The Composition and Diversity of Soil Bacterial and Fungal Communities Along an Urban-To-Rural Gradient in South China

Forests 2019, 10(9), 798;

Drivers of the Distribution of Ecological Species Groups in Temperate Deciduous Managed Forests in the Western Carpathian Mountains
National Forest Centre, Institute for Forest Resource and Information, Department of Remote Sensing, Sokolska 2, 96001 Zvolen, Slovakia
Comenius University in Bratislava, Faculty of Natural Sciences, Department of Ecology, Ilkovicova 6, 84215 Bratislava, Slovakia
Comenius University in Bratislava, Faculty of Natural Sciences, Department of Physical Geography and Geoecology, Ilkovicova 6, 84215 Bratislava, Slovakia
Ministry of Agriculture and Rural Development of the Slovak Republic, Dobrovicova 12, 81266 Bratislava, Slovakia
Constantine the Philosopher University in Nitra, Faculty of Natural Sciences, Department of Ecology and Environmental Sciences, 94901 Nitra, Slovakia
Constantine the Philosopher University in Nitra, Faculty of Natural Sciences, Department of Mathematics, 94901 Nitra, Slovakia
Palacky University, Faculty of Science, Department of Development and Environmental Studies, 17 Listopadu 12, 77146 Olomouc, Czech Republic
Author to whom correspondence should be addressed.
Received: 4 August 2019 / Accepted: 9 September 2019 / Published: 12 September 2019


Managed broadleaf deciduous forests are an important type of forest vegetation in Central Europe, also in the Western Carpathians. These forests are both economically and environmentally valuable. However, little is known about ecological species groups and the inter-specific associations of dominant species in temperate deciduous managed forests in Central Europe. Since the forest stands are in a managed landscape, they are not consistent with the traditionally recognized and used vegetation associations in the Western Carpathians. For these reasons our research contributes to understanding the consequences of broadleaf deciduous forest management. The aim of this research was the determination of ecological species groups and an investigation into the main environmental drivers, in order to explain the distribution of ecological species groups. The numerical TWINSPAN classification was selected to distribute 146 relevés to the five ecological species groups. Of these, 77 relevés were divided into two groups with Fagus sylvatica dominant, while 63 relevés were Quercus petraea dominant. Carpinus betulus, Tilia cordata and Fraxinus excelsior were dominant in 19 relevés. Constrained Analysis of Principal Components was used to explain the vegetation–environment relationship on three transects in the Male Karpaty Mountains. Altitude, pH, Ca, C, K and Mg were selected as the significant environmental drivers responsible for a large part of the species group variability (31.8%). The main requirement for sustainable forest management is knowledge of the vegetation–environment relationship and this research was focused on gaining such understanding. This knowledge can be used as a decision support tool for sustainable management in managed deciduous forests.
herbaceous species; classification; soil properties; topography properties; statistical analysis; systematic sampling; Slovakia

1. Introduction

Knowledge of species–habitat relationships is important in understanding vegetation patterns in forested landscapes [1]. Those relationships are also an important topic within the framework of the assessment of protected areas and their effectiveness in the conservation of forest vegetation biodiversity [2,3,4]. In Central Europe, studies on interactions between forest vegetation and environment have been focused on various parameters, such as the niche breadth of tree species under the soil nutrient [5]; forest vegetation and land-use changes [6]; forest vegetation to topographical-soil gradient [7]; beech and spruce forest to soil chemical properties [8]; and environmental controls of plant species richness [9,10].
Deciduous temperate forest vegetation–environment relationships have been studied globally across various patterns along geographic and environmental gradients [11,12,13,14,15].
The existing vegetation is a result of the complex interaction of historic and recent environments and human disturbance factors [16]. Relationships between environment and plant community have often been studied in areas where human disturbance is minimal, such as in protected areas [17]. Only a few studies have taken place in areas with human disturbance [18]. Disturbance may sometimes override the site's influence, especially in forested areas where human disturbances have a long history and play a key role in land-use changes.
Broadleaf deciduous forests are the dominant natural vegetation of Central Europe [19]. The most important broadleaf deciduous forests across Europe, especially Central Europe, are a mixture of either beech and oak forests or beech-dominated forests, and they are important from ecological and socio-economic points of view [20]. This also applies to the forests of Slovakia, which mostly consist of broadleaf deciduous species (63%), although some forested areas at higher altitudes are dominated by coniferous tree species (37%). The dominant broadleaf deciduous species are European beech (Fagus sylvatica) and Sessile oak (Quercus petraea agg.). Of those forests, 73% are managed and only 23% are not disturbed by human impact (e.g., forests in protected areas).
The concept of ecological species groups is useful in classifying natural communities, determining changes in vegetation, understanding vegetation distribution and environmental factors, estimating species niches, calibrating indicator values for species, modelling the potential distribution of species and plant communities, and assessing habitat quality [21]. The challenge for research into intensively managed forests is to correctly classify forest stands into species groups, because the traditional phytosociological classification was created for forests with a minimal impact from forest management. For this reason, we used the ecological species groups (ESGs) concept as suggested by the study [22]: ESGs are comprised of plants that repeatedly occur together when certain combinations of site factors occur under certain type of forest management. They are species that are perceived to have similar ecological requirements and tolerances as regards environmental stresses and limitations. ESGs are detected by their species composition and abundance patterns among sampling plots. ESG-associated species have similar environmental features. These groups help with the descriptions and the mapping of forest ecosystems in the field through their presence or absence and by the relative coverage of plants in each group.
Forest management consists of anthropogenic disturbances which are able to modulate ecological features [23]. Forest management generally affects abiotic factors in deciduous forests [24], such as microclimate [25,26] and soil nutrients content and dynamics [27]. Tree cutting and coppicing are the most widespread management regimes which affect forest composition, structure and recovery, especially in southern European deciduous forests [28], where mature and old growth forests are rare. On the other hand, growth managed forests in Central Europe occupy a significant area and certain parts of them are both economically and environmentally valuable. Despite the ecological research mainly focusing on the remnants of primeval forests or forest habitats with lower human impact [29,30,31], some local studies also deal with various aspects of managed temperate forests ecology [32,33,34]. As indicated in some studies [35,36], there are ESGs of herbaceous species in lowland coppice forests. Thus, we presumed that other types of forest management also create a basic ecological framework for ESGs of herbaceous species.
The main aim of this study was to investigate the relationship between forest herbaceous vegetation and environment in a forested landscape in the Western Carpathians (Slovakia). In this area, clear-cutting forest management has been in progress since the end of 18th century without any significant changes in land-use to present [37]. This unifying long-term forest management enabled this study to focus on the natural drivers behind and the classification of ecological herbaceous species groups in managed temperate deciduous forests, in order to improve our understanding of the distribution of ESGs as a potential support tool for sustainable forest management.

2. Materials and Methods

2.1. Study Area

The study area is located in a forested landscape in the Male Karpaty Mountains (Figure 1), which are part of the Western Carpathians in the western part of Slovakia. The vegetation consists of broadleaf deciduous forest with the dominant trees: Fagus sylvatica, Quercus petraea agg., Carpinus betulus, Tilia cordata and Acer pseudoplatanus. The climate is temperate, the annual precipitation is 760 mm and the monthly range is from 40 mm in January to 80 mm in August, with most precipitation falling in the northwest and the least in the southeastern parts of the Male Karpaty Mountains. The mean annual air temperature is 8 °C and ranges from −2.5 °C in January to 18 °C in July. The prevailing wind direction is northwest [38].
These forests are influenced by ungulate browsing, which is not sufficiently limited by large carnivores [39]. Forests in the study area have been influenced by local human activities (grazing, litter raking) since the Middle Ages [40]. The first historical forest management plan in study area, based on clear-cutting of mature forests [41], was established in 1761. Currently, all forest stands in the study area are still managed by clear-cutting forest system. Since the forest management practice is unitary in the entire study area, we did not consider it as a variable in our analyses.

2.2. Study Plots

We used a random systematic 200 m × 200 m grid sampling plan to establish 186 study plots. Each study plot was 400 m2 in area. They were situated in floristically and ecologically homogenous mature forest stands (Figure 1). The study plots were located on slopes, mid-slopes and summits of hills, at elevations between 200 m and 580 m above see level. The prevailing soil types in the study area are cambisol and rendzic leptosol. The geological substrate predominantly consists of granitic rocks and calcareous limestone.

2.3. Vegetation Sampling

The final vegetation database contains, after the removal of 40 study plots (forest cutting during the research period), information about 146 vegetation relevés, with a total of 106 species. In the plots (400 m2) the vascular species in each vegetation layer were recorded. Broadleaf deciduous forests in Central Europe, especially in Slovakia, are characterized by different herb species in summer and in spring. For this reason, we recorded herb species in summer (June and July 2016) and in spring (April and May 2017). The cover of each species was visually evaluated using the Braun–Blanquet approach [42]. Each vegetation relevé was processed in TURBOVEG [43] and JUICE 7 [44] software.

2.4. Soil Samplings

In each study plot, soil samples were taken to evaluate the selected chemical characteristics of soil, which can be important as drivers for forest herbaceous species distribution [45]. The soil samples were collected from the upper soil layer, a maximum of 30 cm from the centre of the plot and from two corners (northwest and southeast). Every sample was collected in September, when the weather was stable and chemical properties were also relatively stable. Samples from the corners and the centre were mixed together with a generous one average sample per plot. The samples were then air-dried, homogenized and sieved through a 2 mm mesh. Soil acidity (pH) was measured in KCl (1:2.5 soil/KCL). The total nitrogen (N) was determined by the Kjedahl method. The organic carbon (C) contents were measured by spectrophotometry. The X-ray spectrometry (XRF) technique allowed fast and accurate simultaneous analysis of many elements from each soil sample [46]. The total amounts of aluminum (Al), calcium (Ca), iron (Fe), magnesium (Mn), lead (Pb), potassium (K), sulfur (S), silicon (Si) and zinc (Zn) were measured by the Delta professional XRF spectrometer. Each sample was analyzed five times using the XRF spectrometer, and subsequently the contents of selected variables were calculated by arithmetic means. The main advantages of XRF analysis are the limited preparation required for samples, the non-destructive analysis, the increased total speed and throughput, and the lower start-up and running costs [47].

2.5. Topographical Variables

We selected topographical variables, which can explain forest herbaceous species distribution [48]: Altitude (El), slope (Sl), aspect, profile curvature (PrC), plane curvature (PlC), total curvature (TC), potential global year solar radiation (SR), topographical wetness index (TWI), vertical distance to relief channel network (VDChN), slope height (SH), mid slope position (MSP) and topographical position (TPI). In each study plot a topography characteristic was computed in SAGA GIS 2.1.2. The input data for topography characteristics was digital terrain model 1m (DTM) from Lidar data Leica ALS 70/cm. Subsequently, selected topographical variables were derived from DTM. Each topographical variable was derived in SAGA GIS (2.1.2). Aspect was converted to a southness (South) index and eastness (East) index. The southness and eastness indices were converted by:
ϕ s n =   cos ( a s p e c t )
ϕ e w =   sin ( a s p e c t )
Consequently, the values of φsn and φew range from −1 to 1 and represent the range to which a slope aspects south (φsn = 1), north (φsn = −1), east (φew = 1), or west (φew = −1) [49].

2.6. Statistical Analysis

A modified two-way indicator species analysis (TWINSPAN) [50] was used to classify the 146 relevés into ESGs with similar species abundance patterns. A TWINSPAN analysis was computed in JUICE 7 [44]. Pseudo-species cut levels were set to 0, 5, 25 and 50. Five relevés were selected as a minimum group size for division and a number of ecological species groups were chosen by Sørensen distance and expert view. The fidelity of species to clusters and diagnostic species for vegetation units was calculated using the phi-coefficient based on presence/absence data [51]. In our study, we considered a species characteristic if phi ≥ 0.25. Fisher’s exact test (p < 0.05) was used to reject the fidelity of species with a non-significant occurrence pattern.
The input vegetation, soil and topography data were measured on different scales. We standardized data before other statistical analysis using a natural logarithm or arcsines.
The non-parametric Spearman rank correlation analysis was applied for testing relationships between all study variables. The significant correlation of some environmental variables, especially between Pb, Zn, Fe, Al, S, TPI and VDChN, were indicated by the correlation matrix (Appendix A). Soil contents of S and Al are closely related to Mg as well as Ca. Therefore, these elements were not used in the model of the residual effect of explanatory variables in the species structure. For the same reason Pb, Fe, TPI and VDCnN were excluded from the following analysis.
Explanation of the structure of the ESG–environment relation was measured using Constrained Analysis of Principal Coordinates (CAP) [52]. The CAP techniques were performed in Vegan package of the R 3.1.0 [53] software environment. The selection of significant factors which created the best ordination gradient was made by forward selection and the Monte Carlo permutation test (999 unrestricted permutations were used). The distance matrix was calculated using the Jaccard coefficient of similarity. Constrained Analysis of Principal Coordinates (CAP) is an ordination method similar to Redundancy Analysis (rda), but it allows non-Euclidean dissimilarity indices. The CAP does not expect multivariate normality, nor does it require a linear relationship between response and explanatory variables. It takes into account the correlation structure in the response data cloud without standardization of the original variables by their variance-covariance matrix. The CAP is a two-step procedure, combining two existing multivariate techniques: classical metric multi-dimensional scaling followed by classical canonical analysis, the Canonical Correlations Analysis on unscaled orthonormal principal componential axes.
The significance of differences among the clusters was tested in combination one-way ANOVA and post-hoc Tukey test in the R 3.1.0 (significant level p < 0.05).

3. Results

3.1. Ecological Species Group

The total of 146 relevés was grouped by TWINSPAN analysis into five ecological species groups (Table 1). The main ESG shows a wide range of variation in stand structure, species composition and affinity to environmental characteristics.
The first of the five groups was dominated by Fagus sylvatica, indicated by Luzula luzuloides, Moehringia trinervia. Tithymalus amyglaoides was included in 29 samples. Dentaria bulbifera and Fagus sylvatica were the indicator species of the second group, consisting of 48 samples. The third group, with 10 samples, contained Quercus petraea, Carpinus betulus and Tilia cordata. In herb layers Melica uniflora, Galium sylvaticum and Impatiens parviflora were dominant. Tilia cordata, Fraxinus excelsior, Corydalis cava and Polygonatum multiforum were dominant species in the fourth group of 19 samples. The fifth group was mostly covered by a mix of Carpinus betulus and Quercus petraea with the dominant herbs Moehringia trinervia, Urtica dioica, Mycelis muralis and Ficaria bulbifera present in 43 samples.

3.2. Ecological Species Group-Environment Relation

In order to eliminate variables in the CAP we selected six environmental factors (Ca, K, Mg, pH, C and altitude) which significantly affected the gradient of the ordination axes (Figure 2). The variables explained 18.67 (33.92%) of the total variability in the database of the ESG. The first two axes of CAP explained 31.8% of the total variability in the original dissimilarity matrix and 93.7% of all constrained axes. The first of the two axes were correlated with altitude, while the second axis reflected the changes in the chemical parameters of the soil. All CAP models were highly significant (pseudo-F = 11.892 and p ≤ 0.001).
The five ESG were significantly different in their associations with selected environmental variables in relation to soil and topography factors (Table 2). From the details above it is possible to postulate the following: Altitude can be an important factor in distinguishing between ESG 2 (Fagus sylvatica and Dentaria bulbifera) and ESG 5 (Quercus petraea agg. and Moehringia trinervia). ESG 5 was localized in the lowest parts of the analyzed area and ESG 2 in the highest. The other ESGs were situated at the same altitude, but differ in soil chemistry. In the first ESG (Fagus sylvatica and Luzula luzuloides) there was typically the highest soil reaction and also the lowest contents of nutrients (C) compared to the other analyzed groups. ESG 4 (Tilia cordata and Fraxinus excelsior) can be separated from other ESGs based on the lower mineral content of elements K, Ca and Mg. On the other hand, in ESG 4 it was possible to find the highest content of C. ESG 3 (Quercus petraea agg. and Melica uniflora) can be described as a group with a lower C content compared to ESG 4, and also because of the higher content of chemical mineral nutrients such as K, Ca and Mg.

4. Discussion

In Europe, there have been some classifications of natural forest habitats developed traditionally (since of the beginning of the 20th century). Phytosociological classification (the so-called Zurich–Montpellier approach) is the well-known and widely applying classification system of natural plant communities [42]. Specifically, geobiocenology has been used in Central and East Europe as a classification system focused on natural forests [54]. Recently, CORINE [55] and EUNIS [56] classification systems have been developed. The newest classification system of natural habitats based on vegetation mapping is a classification system under Natura 2000 European network [57], which is developed in detail in some European countries by creating of national catalogues of natural habitats (in Slovakia, see [68]). Many studies [58,59,60,61,62,63] have analyzed the impact of various environmental variables on plant species in the natural forests of Slovakia, but only 23% of forests in Slovakia are non-managed natural or semi-natural forests. However, most of our understanding of forest vegetation–site relationships in Slovakia comes from studies performed within forest ecosystems that are relatively undisturbed by humans or from investigations into the effects of particular management strategies on a small scale [64,65]. If we take into account a human impact on forest ecosystems, including land-use change and modifications in the structure of the landscape, it is important to identify the primary driving forces of diversity, not only in undisturbed ecosystems, but also across entire landscapes that have been actively and intensively managed for many years [66,67]. The need for research into the intensively managed forests will grow with the decrease of natural forests in the future, because some of the natural forests in Slovakia are not included in protected areas. In unmanaged forests in strictly protected areas with similar altitude and soil composition, the expected traditional vegetation unit would be predominantly habitats of Acidophilous oak forests, Asperulo-Fagetum beech forests, Luzulo-Fagetum beech forests, and Medio-European limestone beech forests [68]. These vegetation units of forest natural habitats can only be used for mapping and research of natural forests, because the definition of these units is based on both natural structure and species diversity. Our research indicates that when these traditional units of natural forests are disturbed by clear-cutting forest management, it may revert or regenerate into a different vegetation types, such as identified ESGs in the study area.
On the base of TWINSPAN we have identified five species groups and established a list of diagnostic species. This species grouping was not consistent with the traditionally recognized units in the territory of the Western Carpathians [69]. The author of the study [70] found relationships between traditionally used vegetation units in Slovakia and vegetation units created by numerical classifications, but these were in natural or near-natural forest stands. The fact that the numerical classification vegetation units were not consistent with the traditional vegetation units was identified by the study [71]. ESG 1 was statistically similar to Luzulo-fagion and ESG 2 was also similar to Eu-fagenion, but there were no accurate classifications because some diagnostic species were missing. ESG 3 and ESG 5 were very similar to Caricipilosae-Carpinenionbetuli, but ESG 5 had no typical diagnostic species, Moehringia trinervia. Only ESG 4 was relatively well classified by floristic composition and ecology as Tilio-Acerion.
The main problems with the inclusion of traditional vegetation units were: (1) We did not choose ideal forest stands; (2) we did not carry out research into natural forest stands, but we chose intensively managed forest landscapes, because they are the predominant type of forest in Central Europe, especially in Slovakia; (3) the forest stands have been without the direct influence of management for five years, but they were near the stands where management had a direct influence (logging, path or forest road). An example of this influence was the high amount of Urtica dioica, which is not a typical forest herb.
Altitude and soil chemistry played a major role in the ecological species groupings. The highest variation of vegetation was explained by altitude, K and pH [9]. Study of [5] revealed Mg, K and Ca as limiting factors for plant growth in temperature beech forests. These results were expected in accordance with general knowledge on abiotic factors importance in managed forests [72] and local knowledge in Slovakia [73,74].
Altitude had a major role in explaining the variance in vegetation [75,76]. On the high-altitude forest stands only a few species are capable of growth in the characteristically harsh climate, which has lower temperatures, higher wind speeds and more drastic changes in the type and amount of precipitation. Altitude is generally known as an important factor in natural forest vegetation distribution in temperate mountains in the form of forest vegetation zones [77]. But, in managed forests, vegetation zonation is disturbed by both human activities including forest management practice and climate change impacts [78].
Soil pH played a major role in the separation of ESG 1. It was one of the most important factors affecting the plant community and showed the important role of pH in the separation of species groups [18,21]. The pH only had a minor role in a few studies [79,80]. Soil organic C played a major role in the separation of ESG 4. It had a high absorption capability, which increased the soil´s exchange capacity and therefore its fertility levels. It was an important factor in the variety of deciduous forest in China [81]. Calcium was an important factor in the separation of ESG 3 and ESG 4. Plants use calcium to activate certain enzymes and to send signals that coordinate cellular activities, and it is also responsible for holding together the cell walls. Calcium played a significant role in the separation of species and species groups [58]. Potassium played a major role in the separation of ESG 3. The presence of potassium in the soil makes it easy to transform the water and nutrients in the soil, and it plays a major role in the regulation of photosynthesis, carbohydrate transport, protein synthesis and other phyto-sociological processes. Study [21] showed the importance of potassium in the separation of species groups as well. Authors of the study [82] found potassium as one of the effective factors in the distribution of vegetation types. Magnesium was an important micronutrient in the separation of ESG 4. It is necessary for normal plant growth and has an important role in photosynthesis. Thus, our results are in accordance with the study by [82], which clearly indicated the important role of magnesium in the separation of species groups.

5. Conclusions

We have evaluated the relationship between some environmental drivers and vegetation of managed forests dominated by Fagus sylvatica and Quercus petraea in Slovakia. We found that altitude and soil's chemical properties were effective in the definition of five ecological species groups in the Male Karpaty Mountains. Soil pH, organic calcium, potassium and magnesium were important factors in the separation of individual ecological species groups. Altitude also played a major role in the variance of vegetation in lower mountains of the study area. These results indicate that detailed vegetation research aimed to ecological species groups in deciduous managed forest of Central Europe produces important information for assessment of forest management suitability for herbaceous species and support decision-making in temperate forest restoration, management and planning.

Author Contributions

M.G., P.B. and F.P. prepared a study design; methodology was developed by V.F., I.M. and I.M.; V.F. and L.K. were responsible for statistical analyses and D.V. was responsible for validation of statistics; field investigation was done by M.G., P.B., V.F., I.M. and F.P.; F.P. and I.M. wrote an original draft; I.M. was responsible for review and editing; project administration was done by M.G. and F.P.


The publication was supported by Slovak Research and Development Agency–grant number APVV-15-0597 Use of geoecological data in the implementation of precision agriculture and, Scientific Grant Agency of the Ministry of Education of Slovak Republic and Slovak Academy of Science–grant number 1/0247/19 Assessment of land-use dynamics and land cover changes and, Cultural and Educational Grant Agency of the Slovak Republic–grant number 032UKF-4/2018 Overview of Methods and Proposal for the Application of the Ecosystem Services Concept in the Environmental Studies Study Program.

Conflicts of Interest

The authors declare no conflict of interest.

Appendix A

Table A1. Spearman rank correlation matrix for environmental variables. Red p < 0.05; green p < 0.01; orange p < 0.001.
Table A1. Spearman rank correlation matrix for environmental variables. Red p < 0.05; green p < 0.01; orange p < 0.001.
Fe 1.00000.1418−0.29700.0808−0.2647−0.25090.13890.5087−0.0400−0.15540.60550.0551−0.0553−0.02320.00330.0737−0.0382−0.0625−0.10800.16480.0514−0.00430.1182
Ca 1.00000.34500.4706−0.48920.40250.30780.2603−0.09040.4103−0.31890.1113−0.03830.04440.2571−0.02390.1373−0.1349−0.19410.0479−0.1371−0.01490.1075
K 1.00000.6300−0.46240.96610.44400.03470.01280.1833−0.3549−0.13770.04090.08590.1680−0.02520.11790.1195−0.0447−0.2772−0.03100.04490.0460
Al 1.0000−0.14770.71340.70810.1094−0.23730.1513−0.33840.0908−0.00570.06510.16690.02310.12430.0407−0.03590.02120.0025−0.07170.0643
Si 1.0000−0.4523−0.0188−0.5817−0.19080.0467−0.18120.27630.0371−0.1072−0.11500.0753−0.1649−0.02240.13900.20800.0704−0.0917−0.1608
S 1.00000.50110.0943−0.02190.1656−0.3532−0.11600.04670.11190.1927−0.03940.16020.0995−0.0341−0.2221−0.03730.02030.0690
Mg 1.00000.0468−0.09370.1158−0.18410.1099−0.09730.00120.11080.0163−0.0139−0.0140−0.00920.02070.0521−0.05620.0413
C 1.00000.1012−0.45760.4951−0.09880.06820.12340.0560−0.02900.17760.0651−0.05350.05010.0525−0.01670.2388
N 1.0000−0.14980.1807−0.3186−0.1921−0.0626−0.1096−0.1757−0.08020.0473−0.0439−0.2707−0.12020.25570.1083
pH 1.0000−0.51750.1485−0.0507−0.06940.2624−0.0768−0.0129−0.1274−0.18480.0072−0.25840.0814−0.0787
El 1.0000−0.13970.0272−0.0778−0.22320.05620.05790.08250.05570.15850.2818−0.01500.1520
Sl 1.0000−0.0079−0.12760.3536−0.1355−0.2181−0.1003−0.11270.1903−0.1513−0.1281−0.0240
PrC 1.00000.2376−0.0903−0.00570.29010.08110.03180.18910.07340.03010.1084
PlC 1.0000−0.1194−0.11910.1554−0.08440.04880.09000.0174−0.02000.0223
TC 1.0000−0.1813−0.1406−0.0162−0.0140−0.1918−0.29560.00950.0159
TWI 1.0000−0.09380.0166−0.10050.02660.3862−0.1172−0.1858
TPI 1.0000−0.11330.23130.57280.08020.07630.6302
East 1.00000.0709−0.17870.2024−0.1752−0.0976
Sout 1.00000.07270.07850.0268−0.0058
SH 1.00000.1088−0.08460.4594
SR 1.0000−0.2085−0.0650
MSP 1.00000.1340


  1. Solon, J.; Degórski, M.; Roo-Zielińska, E. Vegetation response to a topographical-soil gradient. Catena 2007, 71, 309–320. [Google Scholar] [CrossRef]
  2. Oprsal, Z.; Harmacek, J.; Pavlik, P.; Machar, I. What Factors can Influence the Expansion of Protected Areas around the World in the Context of International Environmental and Development Goals? Probl. Ekorozw. 2018, 13, 145–157. [Google Scholar]
  3. Pechanec, V.; Machar, I.; Pohanka, T.; Opršal, Z.; Petrovič, F.; Švajda, J.; Šálek, L.; Chobot, K.; Filippovova, J.; Cudlín, P.; et al. Effectiveness of Natura 2000 system for habitat types protection: A case study from the Czech Republic. Nat. Conserv. 2018, 24, 21–41. [Google Scholar] [CrossRef]
  4. Machar, I. Conservation and Management of Floodplain Forests in the Protected Landscape Area Litovelske Pomoravi (Czech Republic) Introduction. In Conservation and Management of Floodplain Forests in the Protected Landscape Area Litovelske Pomoravi (Czech Republic); Machar, I., Ed.; Palacky University: Olomouc, Czech Republic, 2009; pp. 7–108, Accession Number: WOS: 000331015800001; ISBN 978-80-244-2355-5. [Google Scholar]
  5. Leuschner, C.; Meier, I.C.; Hertel, D. On the niche breadth ofFagus sylvatica: Soil nutrient status in 50 Central European beech stands on a broad range of bedrock types. Ann. For. Sci. 2006, 63, 355–368. [Google Scholar] [CrossRef]
  6. Kilianová, H.; Pechanec, V.; Brus, J.; Kirchner, K.; Machar, I. Analysis of the development of land use in the Morava River floodplain, with special emphasis on the landscape matrix. Morav. Geogr. Rep. 2017, 25, 46–59. [Google Scholar]
  7. Chmura, D. The slope aspect affects the heterogenity and growth of ground vegetation in deciduous forest. Pol. J. Ecol. 2008, 56, 463–470. [Google Scholar]
  8. Langenbruch, C.; Helfrich, M.; Flessa, H. Effects of beech (Fagus sylvatica), ash (Fraxinus excelsior) and lime (Tilia spec.) on soil chemical properties in a mixed deciduous forest. Plant Soil 2012, 352, 389–403. [Google Scholar] [CrossRef]
  9. Slezak, M.; Hrivnak, R.; Machava, J. Environmental controls of plant species richness and species composition in black alder floodplain forests of central Slovakia. Tuexenia 2017, 37, 79–94. [Google Scholar] [CrossRef]
  10. Simon, J.; Machar, I.; Brus, J.; Pechanec, V. Combining a growth-simulation model with acoustic-wood tomography as a decision-support tool for adaptive management and conservation of forest ecosystems. Ecol. Inform. 2015, 30, 309–312. [Google Scholar] [CrossRef]
  11. Merino, A.; Real, C.; Álvarez-González, J.G.; Rodríguez-Guitián, M.A. Forest structure and C stocks in natural Fagus sylvatica forest in southern Europe: The effects of past management. For. Ecol. Manag. 2007, 250, 206–214. [Google Scholar] [CrossRef]
  12. Shen, Z.H.; Fang, J.Y.; Chiu, C.A.; Chen, T.Y. The geographical distribution and differentiation of Chinese beech forests and the association with Quercus. Appl. Veg. Sci. 2015, 18, 23–33. [Google Scholar] [CrossRef]
  13. Cerny, T.; Kopecky, M.; Petrik, P.; Song, J.; Srutek, M.; Valachovic, M.; Altman, J.; Dolezal, J. Classification of Korean forests: Patterns along geographic and environmental gradients. Appl. Veg. Sci. 2015, 18, 5–22. [Google Scholar] [CrossRef]
  14. Rad, J.E.; Shafiei, A.B. The distribution of ecological species groups in Fagetum communities of Caspian forests: Determination of effective environmental factors. Flora Morphol. Distrib. Funct. Ecol. Plants 2010, 205, 721–727. [Google Scholar] [CrossRef]
  15. Boyle, M.F.; Abella, S.R.; Shelburne, V.B. An ecosystem classification approach to assessing forest change in the southern Appalachian Mountains. For. Ecol. Manag. 2014, 323, 85–97. [Google Scholar] [CrossRef]
  16. Hoersch, B.; Braun, G.; Schmidt, U. Relation between landform and vegetation in alpine regions of Wallis, Switzerland. A multiscale remote sensing and GIS approach. Comput. Environ. Urban Syst. 2002, 26, 113–139. [Google Scholar] [CrossRef]
  17. Machar, I.; Simon, J.; Rejsek, K.; Pechanec, V.; Brus, J.; Kilianova, H. Assessment of Forest Management in Protected Areas Based on Multidisciplinary Research. Forests 2016, 7, 285. [Google Scholar] [CrossRef]
  18. Brosofske, K.; Chen, J.; Crow, T. Understory vegetation and site factors: Implications for a managed Wisconsin landscape. For. Ecol. Manag. 2001, 146, 75–87. [Google Scholar] [CrossRef]
  19. Willner, W.; Di Pietro, R.; Bergmeier, E. Phytogeographical evidence for post-glacial dispersal limitation of European beech forest species. Ecography 2009, 32, 1011–1018. [Google Scholar] [CrossRef]
  20. Machar, I. Attempt to summarize the problems: Is a sustainable management of floodplain forest geobiocenoses possible. In Biodiversity and Target Management of Floodplain Forests in the Morava River Basin (Czech Republic); Machar, I., Ed.; Palacky University: Olomouc, Czech Republic, 2010; pp. 189–226. ISBN 978-80-244-2530-6. [Google Scholar]
  21. Adel, M.N.; Pourbabaei, H.; Dey, D.C. Ecological species group—Environmental factors relationships in unharvested beech forests in the north of Iran. Ecol. Eng. 2014, 69, 1–7. [Google Scholar] [CrossRef]
  22. Host, G.E.; Pregitzer, K.S. Ecological species groups for upland forest ecosystems of northwestern Lower Michigan. For. Ecol. Manag. 1991, 43, 87–102. [Google Scholar] [CrossRef]
  23. Decocq, G.; Aubert, M.; Dupont, F.; Bardat, J.; Wattez-Franger, A.; Saguez, R.; De Foucault, B.; Alard, D.; Delelis-Dusollier, A. Silviculture-driven vegetation change in a European temperate deciduous forest. Ann. For. Sci. 2005, 62, 313–323. [Google Scholar] [CrossRef]
  24. Hansen, A.; Rotella, J. Abiotic factors. In Maintaining Biodiversity in Forest Ecosystems; Malcolm, L., Hunter, J.R., Eds.; Cambridge University Press: Cambridge, UK, 1999; pp. 161–209. ISBN 0-521-63104-1. [Google Scholar]
  25. Ivanova, M.; Michaeli, E.; Boltiziar, M.; Fazekasova, D. The analysis of changes ecological stability of landscape in the contrasting region of the mountain range and a lowland. In Proceedings of the International Multidisciplinary Scientific GeoConference: SGEM: Surveying Geology & Mining Ecology Management, Albena, Bulgaria,, 16–22 June 2013. [Google Scholar]
  26. Belčáková, I. The impact of floodplain vegetation on the erosion-sedimentation processess in fluvisols during flood events. Appl. Ecol. Environ. Res. 2019, 17, 3. [Google Scholar] [CrossRef]
  27. Thomas, P.A.; Packham, J.R. Nutrients dynamics in different forests. In Ecology of Woodland and Forests; Thomas, P.A., Packham, J.R., Eds.; Cambridge University Press: Cambridge, UK, 2007; pp. 341–345. ISBN 978-0-521-83452-0. [Google Scholar]
  28. De Nicola, C.; Fanelli, G.; Testi, A.; Costa, C.; D’Angeli, D.; Pignatti, S. Recovering ability of deciduous Oak Forests after different stages of tree cutting in Central Italy. Rend. Lincei 2017, 28, 53–64. [Google Scholar] [CrossRef]
  29. Roo-Zelinska, E. Ecological groups of vascular plant species in the herb layer of the pine forests of Northern and Central Europe. Pol. J. Ecol. 2003, 51, 493–506. [Google Scholar]
  30. Ujhazyova, M.; Ujhazy, K.; Chytry, M.; Williner, W.; Ciliak, M.; Malis, F.; Slezak, M. Diversity of beech forests vegetation it the Eastern Alps, Bohemian Massif and the Western Carpathians. Preslia 2016, 88, 435–457. [Google Scholar]
  31. Zastocki, D.; Lachowicz, H.; Sadowski, J.; Moskalik, T. Changes in the Assortment and Species Structure of Timber Harvested from the Polish Managed Part of Białowieża Forest. Sustainability 2018, 10, 3279. [Google Scholar] [CrossRef]
  32. Szymura, T.H.; Murak, S.; Szymura, M.; Raduła, M.W. Changes in forest cover in Sudety Mountains during the last 250 years: Patterns, drivers, and landscape-scale implications for nature conservation. Acta Soc. Bot. Pol. 2018, 87, 3576. [Google Scholar] [CrossRef]
  33. Machar, I.; Schlossarek, M.; Pechanec, V.; Uradnicek, L.; Praus, L.; Sıvacıoğlu, A. Retention Forestry Supports Bird Diversity in Managed, Temperate Hardwood Floodplain Forests. Forests 2019, 10, 300. [Google Scholar] [CrossRef]
  34. Schulze, E.D.; Bouriaud, O.; Weber, U.; Roscher, C.; Hessenmoeller, D.; Kroiher, F.; Schall, P. Management breaks the natural productivity-biodiversity relationship in forests and grassland: An opinion. For. Ecosyst. 2018, 5, 3. [Google Scholar] [CrossRef]
  35. Řepka, R.; Šebesta, J.; Maděra, P.; Vahalík, P. Comparison of the floodplain forest floristic composition of two riparian corridors: Species richness, alien species and the effect of water regime changes. Biologia 2015, 70, 208–217. [Google Scholar] [CrossRef]
  36. Madera, P.; Machala, M.; Slach, T.; Friedl, M.; Cernušáková, L.; Volarík, D.; Buček, A. Predicted occurrence of ancient coppice woodlands in the Czech Republic. iForest-Biogeosci. For. 2017, 10, 788–795. [Google Scholar] [CrossRef]
  37. Hresko, J.; Petrovič, F.; Misovicova, R. Mountain landscape archetypes of the Western Carpathians (Slovakia). Biodivers. Conserv. 2015, 24, 3269–3283. [Google Scholar] [CrossRef]
  38. Mikulova, K.; Stastny, P.; Bochnicek, O.; Borsanyi, P.; Cepcekova, E.; Ondruska, P. Klimatologické Normály Teploty Vzduchu na Slovensku [Climate in Slovakia]; SHMU: Bratislava, Slovensko, 2015; p. 135. [Google Scholar]
  39. Kovařík, P.; Kutal, M.; Machar, I. Sheep and wolves: Is the occurrence of large predators a limiting factor for sheep grazing in the Czech Carpathians? J. Nat. Conserv. 2014, 22, 479–486. [Google Scholar] [CrossRef]
  40. Machar, I.; Vozenilek, V.; Simon, J.; Pechanec, V.; Brus, J.; Fulnecek, P.; Vitek, T. Joining of the historical research and future prediction as a support tool for the assessment of management strategy for European beech-dominated forests in protected areas. Nat. Conserv. 2017, 22, 51–78. [Google Scholar] [CrossRef]
  41. Kimmins, J.P.; Keenan, R.J. The ecological effects of clear-cutting. Environ. Rev. 1993, 1, 121–144. [Google Scholar]
  42. Braun-Blanquet, J.; Fuller, G.D.; Conard, H.S. Plant Sociology, the Study of Plant Communities, 1st ed.; McGraw-Hill Book Company: New York, NY, USA; London, UK, 1932; p. 476. [Google Scholar]
  43. Hennkens, S.M.; Schaminée, J.H.J. Turboveg, a comprehensive database management system for vegetation data. J. Veg. Sci. 2001, 12, 589–591. [Google Scholar] [CrossRef]
  44. Tichý, L. JUICE, software for vegetation classification. J. Veg. Sci. 2002, 13, 451–453. [Google Scholar] [CrossRef]
  45. Weigel, R.; Gilles, J.; Klisz, M.; Manthey, M.; Kreyling, J. Forest understory vegetation is more related to soil than to climate towards the cold distribution margin of European beech. J. Veg. Sci. 2019, 30, 746–755. [Google Scholar] [CrossRef]
  46. Kubala-Kukus, A.; Banas, D.; Braziewicz, J.; Dziadowicz, M.; Kopec, E.; Majewska, U.; Mazurek, M.; Pajek, M.; Sobisz, M.; Stabrawa, I.; et al. X-ray spectrometry and X-ray microtomography techniques for soil and geological samples analysis. Nucl. Instrum. Methods Phys. Res. Sect. B Beam Interact. Mater. Atoms 2015, 364, 85–92. [Google Scholar] [CrossRef]
  47. Parsons, C.; Grabulosa, E.M.; Pili, E.; Floor, G.H.; Román-Ross, G.; Charlet, L. Quantification of trace arsenic in soils by field-portable X-ray fluorescence spectrometry: Considerations for sample preparation and measurement conditions. J. Hazard. Mater. 2013, 262, 1213–1222. [Google Scholar] [CrossRef]
  48. Svobodova, J.; Vozenilek, V. Relief for models of natural phenomena. In Landscape Modelling: Geographical Space, Transformation and Future Scenarios (Urban and Landscape Perspectives); Anděl, J., Bičík, I., Dostál, P., Shasneshin, S., Eds.; Springer: Dordrecht, The Netherlands, 2010; pp. 183–196. [Google Scholar]
  49. Deng, Y.; Chen, X.; Chuvieco, E.; Warner, T.; Wilson, J.P. Multi-scale linkages between topographic attributes and vegetation indices in a mountainous landscape. Remote Sens. Environ. 2007, 111, 122–134. [Google Scholar] [CrossRef]
  50. Roleček, J.; Tichý, L.; Zelený, D.; Chytrý, M. Modified TWINSPAN classification in which the hierarchy respects cluster heterogeneity. J. Veg. Sci. 2009, 20, 596–602. [Google Scholar] [CrossRef]
  51. Tichý, L.; Chytrý, M. Statistical determination of diagnostic species for site groups of unequal size. J. Veg. Sci. 2006, 17, 809–818. [Google Scholar] [CrossRef]
  52. Anderson, M.J.; Willis, T.J. Canonical analysis of principal coordinates: A useful method of contrained ordination for ecology. Ecology 2003, 84, 511–525. [Google Scholar] [CrossRef]
  53. R Core Team. R: A Language and Environmenta for Statistical Computing; R Foundation for Statistical Computing: Vienna, Austria, 2014. [Google Scholar]
  54. Zlatník, A. Přehled skupin typů geobiocénů původně lesních a křovinných v ČSSR. Zpr. Geogr. Úst. ČSAV 1976, 13, 55–64. [Google Scholar]
  55. Comission of European Communities. Corine biotopes manual. In Habitats of the European Community; Office for Publications of the EC: Luxembourg, 1991; p. 122. [Google Scholar]
  56. Davies, C.E.; Moss, D. EUNIS Habitat Classification. In European Topic Centre on Nature Conservation; European Environment Agency: Paris, France, 1997; p. 98. [Google Scholar]
  57. Miko, L. Nature and landscape protection in the European context. In Ochrana Přírody a Krajiny v České Republice, 1st ed.; Machar, I., Drobilová, L., Eds.; Palacky University Olomouc: Olomouc, Czech Republic, 2012; pp. 43–49. ISBN 978-80-244-3041-6. [Google Scholar]
  58. Jarolímek, I.; Šibík, J.; Hegedüšová, K.; Janišová, M.; Kliment, J.; Kučera, P.; Májeková, J.; Michálková, D.; Sadloňová, J.; Šibíková, I.; et al. A list of vegetation units of Slovakia. In Diagnostic, Constant and Dominant Species of the Higher Vegetation Units of Slovakia, 1st ed; Jarolimek, I., Sibik, J., Eds.; Veda: Bratislava, Slovakia, 2008; pp. 295–329. [Google Scholar]
  59. Petrovič, F. Landscape-ecological optimization of hydric potential in foothills region with dispersed settlements—A case study of nová bošáca, slovakia. Appl. Ecol. Environ. Res. 2017, 15, 379–400. [Google Scholar] [CrossRef]
  60. Súľovský, M.; Falťan, V.; Skokanová, H.; Havlíček, M.; Petrovič, F. Spatial analysis of long-term land-use development in regard to physiotopes: Case studies from the Carpathians. Phys. Geogr. 2017, 25, 1–19. [Google Scholar] [CrossRef]
  61. Skokanova, H.; Havlicek, M.; Klusacek, P.; Martinat, S. Five military training areas—Five different trajectories of land cover development? Case studies from the Czech Republic. Geogr. Cassoviensis 2017, 11, 201–213. [Google Scholar]
  62. Salekl, L.; Sivacioglu, A.; Topacoglu, O.; Zahradnile, D.; Jerabkoval, L.; Machar, I. Crowns of Old Remnant Oak Standards. Fresenius Environmental Bulletin 2017, 26, 4023–4032. [Google Scholar]
  63. Miklós, L.; Izakovičová, Z.; Offertálerová, M.; Miklósová, V. The Institutional Tools of Integrated Landscape Management in Slovakia for Mitigation of Climate Change and Other Natural Disasters. Eur. Countrys. 2017, 9, 647–657. [Google Scholar] [CrossRef]
  64. Lieskovský, J.; Kaim, D.; Balázs, P.; Boltižiar, M.; Chmiel, M.; Grabska, E.; Király, G.; Konkoly-Gyuró, E.; Kozak, J.; Antalová, K.; et al. Historical land use dataset of the Carpathian region (1819–1980). J. Maps 2018, 14, 644–651. [Google Scholar] [CrossRef]
  65. Boltiziar, M.; Olah, B.; Gallay, I.; Gallayova, Z. Transformation of the Slovak cultural landscape and its recent trends. In Proceedings of the 17th International Symposium on Landscape Ecology - Landscape and Landscape Ecology, Nitra, Slovakia, 27–29 May 2015. [Google Scholar]
  66. Munteanu, C.; Kuemmerle, T.; Boltiziar, M.; Lieskovský, J.; Mojses, M.; Kaim, D.; Konkoly-Gyuró, É.; Mackovčin, P.; Műller, D.; Ostapowicz, K.; et al. Nineteenth-century land-use legacies affect contemporary land abandonment in the Carpathians. Reg. Environ. Chang. 2017, 17, 2209–2222. [Google Scholar] [CrossRef]
  67. Machar, I.; Vozenilek, V.; Kirchner, K.; Vlckova, V.; Bucek, A. Biogeographic model of climate conditions for vegetation zones in Czechia. Geografie 2017, 122, 64–82. [Google Scholar]
  68. Stanova, V.; Valachovic, M. Katalog Biotopov Slovenska [Catalogue of Habitats in Slovakia]; Daphne: Bratislava, Slovakia, 2002; ISBN 80-89133-00-2. [Google Scholar]
  69. Slezák, M. Environmental conditions in relation to variability of deciduous forest vegetation — A study from volcanic mountain in central Slovakia. Biologia 2012, 67, 310–322. [Google Scholar]
  70. Knollova, I.; Chytry, M. Oak-hornbeam forests of the Czech Republic: Geographical and ecological approaches to vegetation classification. Preslia 2004, 76, 291–311. [Google Scholar]
  71. Fontaine, M.; Aerts, R.; Özkan, K.; Mert, A.; Gülsoy, S.; Süel, H.; Waelkens, M.; Muys, B. Elevation and exposition rather than soil types determine communities and site suitability in Mediterranean mountain forests of southern Anatolia, Turkey. For. Ecol. Manag. 2007, 247, 18–25. [Google Scholar] [CrossRef]
  72. Wang, J.-J.; Pisani, O.; Lin, L.H.; Lun, O.O.; Bowden, R.D.; Lajtha, K.; Simpson, A.J.; Simpson, M.J. Long-term litter manipulation alters soil organic matter turnover in a temperate deciduous forest. Sci. Total. Environ. 2017, 607, 865–875. [Google Scholar] [CrossRef]
  73. Havlicek, M.; Skokanova, H.; Sarapatka, B.; Netopil, P.; Pavelkova, R. Development of land use of the kyjovska pahorkatina hilly land. Geogr. Inf. 2018, 22, 103–117. [Google Scholar] [CrossRef]
  74. Kozová, M.; Dobšinská, Z.; Pauditšová, E.; Tomčíková, I.; Rakytová, I. Network and participatory governance in urban forestry: An assessment of examples from selected Slovakian cities. For. Policy Econ. 2018, 89, 31–41. [Google Scholar] [CrossRef]
  75. Elith, J.; Leathwick, J.R. Species Distribution Models: Ecological Explanation and Prediction Across Space and Time. Annu. Rev. Ecol. Evol. Syst. 2009, 40, 677–697. [Google Scholar] [CrossRef]
  76. Spulerova, J. The influence of exposition on the succession in a sedge-beech forest. Ekologia 2000, 19, 181–186. [Google Scholar]
  77. Garamvoelgyi, A.; Hufnagel, L. Impacts f climate change on vegetation distribution no.1. Climate change induced vegetation shifts in the Palearctic region. Appl. Ecol. Environ. Res. 2013, 11, 79–122. [Google Scholar] [CrossRef]
  78. Naqinezhad, A.; Hamzeh’ee, B.; Attar, F. Vegetation–environment relationships in the alderwood communities of Caspian lowlands, N. Iran (toward an ecological classification). Flora-Morphol. Distrib. Funct. Ecol. Plants 2008, 203, 567–577. [Google Scholar] [CrossRef]
  79. Moradi, H.; Naqinezhad, A.; Siadati, S.; Yousefi, Y.; Attar, F.; Etemad, V.; Reif, A. Elevational gradient and vegetation-environmental relationships in the central Hyrcanian forests of northern Iran. Nord. J. Bot. 2016, 34, 1–14. [Google Scholar] [CrossRef]
  80. Fu, B.; Liu, S.; Ma, K.; Zhu, Y.-G. Relationships between soil characteristics, topography and plant diversity in a heterogeneous deciduous broad-leaved forest near Beijing, China. Plant. Soil 2004, 261, 47–54. [Google Scholar] [CrossRef]
  81. Jafari, M.; Chahouki, M.; Tavili, A.; Azarnivand, H.; Amiri, G. Effective environmental factors in the distribution of vegetation types in Poshtkouh rangelands of Yazd Province (Iran). J. Arid. Environ. 2004, 56, 627–641. [Google Scholar] [CrossRef]
  82. He, M.; Zheng, J.; Li, X.; Qian, Y. Environmental factors affecting vegetation composition in the Alxa Plateau, China. J. Arid. Environ. 2007, 69, 473–489. [Google Scholar] [CrossRef]
Figure 1. Location of the study areas and detailed view of selected study plot.
Figure 1. Location of the study areas and detailed view of selected study plot.
Forests 10 00798 g001
Figure 2. Results of a Constrained Analysis of Principal Coordinates showing the position of ecological species groups at the first two restricted ordination axes. The gradients of the ordination axes were modelled by significant environmental parameters selected in a stepwise procedure with backward elimination.
Figure 2. Results of a Constrained Analysis of Principal Coordinates showing the position of ecological species groups at the first two restricted ordination axes. The gradients of the ordination axes were modelled by significant environmental parameters selected in a stepwise procedure with backward elimination.
Forests 10 00798 g002
Table 1. Synoptic table of percentage frequency (constancy) and fidelity (phi coefficient, upper indices). Only diagnostic species for specific vegetation groups with phi coefficient ≥0.25 are shown in the table.
Table 1. Synoptic table of percentage frequency (constancy) and fidelity (phi coefficient, upper indices). Only diagnostic species for specific vegetation groups with phi coefficient ≥0.25 are shown in the table.
No. of relevés2948101944
Fagus sylvatica10036,69834,5107939
Luzula luzuloides3452,02
Moehringia trinervia6638,7257751,5
Tithymalus amyglaoides3127,8101111
Dentaria bulbifera5521,06329,41047
Acer pseudoplatanus2214,62021
Acer campestre323021,23730,82
Carpinus betulus9054,8326427,5
Quercus petraea agg.348048,8325017,1
Tilia Cordata6035,37956,32
Galium sylvaticum agg.35063,6
Hedera helix3019,24743,02
Impatiens parviflora368033,58437,75912,5
Melica uniflora10066,57439,17
Galium aparine agg.4023,45845,47
Fraxinus excelsior24256,52
Corydalis cava106368,7
Galium odoratum10104730,34325,3
Geranium robertianum agg.7505322,25019,4
Ficaria bulbifera104731,45034,6
Alliaria petiolata505322,35726,7
Polygonatum multiflorum104251,9
Anemone ranunculoides81625,8
Calystegia sepium agg.7230326139,7
Viola reichenbachiana10111819,3
Mycelis muralis10264539,2
Cerasus avium751622,4
Carex sylvatica4101114,3
Urtica dioica41220117549,4
Rubus fruticosus agg.1714115040,8
Poa nemoralis agg.351625,4
Table 2. Standard deviation of the most important environmental variables between species groups in the study area.
Table 2. Standard deviation of the most important environmental variables between species groups in the study area.
ESG 1ESG 2ESG 3ESG 4ESG 5F-ratiop-value
Ca (%)0.412 ± 0.0690.374 ± 0.0530.653 ± 0.1170.572 ± 0.0850.358 ± 0.0592.2730.064
K (%)1.494 ± 0.0511.377 ± 0.0391.814 ± 0.0851.692 ± 0.0621.716 ± 0.04312.712<0.05
Mg (%)0.595 ± 0.0310.577 ± 0.0230.826 ± 0.0520.723 ± 0.0380.615 ± 0.0266.799<0.05
C (%)1.868 ± 0.1992.435 ± 0.1511.924 ± 0.3342.851 ± 0.2421.509 ± 0.1677.165<0.05
pH3.723 ± 0.1163.604 ± 0.0883.661 ± 0.1953.498 ± 0.1423.558 ± 0.0980.4800.75
El (m)425.752 ± 12.644470.023 ± 9.559287.258 ± 21.159398.017 ± 15.350279.992 ± 10.57952.468<0.05

© 2019 by the authors. Licensee MDPI, Basel, Switzerland. This article is an open access article distributed under the terms and conditions of the Creative Commons Attribution (CC BY) license (
Back to TopTop