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1 November 2018 Long-Term Changes in Dwarf Pine (Pinus mugo Turra) Cover and Growth in the Orava Beskid Mountains, Slovakia
Zuzana Parobeková, Michal Bugala, Miroslav Kardoš, Martin Dovciak, Ivan Lukáčik, Milan Saniga
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Dwarf pine (Pinus mugo Turra) thickets are a substantial land cover in high-elevation mountain ecosystems in Europe, where they fulfill important functions in soil conservation and as wildlife habitat. In many areas across Europe these thickets have rapidly expanded over the past decades because of changing climate and land use, highlighting the need to better understand how species spread relates to growth traits and changing environmental conditions. We quantified changes in dwarf pine cover by elevation on 2 mountains in the Western Carpathians (Central Europe) over 64 years (Babia hora) and 40 years (Pilsko), and we linked them to species growth responses to climate using archival photogrammetry and stem length measurements. We correlated mean growth chronologies with mean monthly temperature and precipitation to assess the main climatic factors driving growth. The total expansion of dwarf pine cover was substantial (28.6% in Babia hora and 57.1% in Pilsko), but the rate of expansion varied with elevation, site, and intra- and interspecific competition. The largest expansion occurred in the open stands of the high elevations (1550–1650 m). Statistically significant positive correlations between growth and temperature were recorded for the most recent growing season and for the preceding growing season. However, despite rising temperatures over time, mean species growth during the last 20 years decreased slightly. The correlation of growth with precipitation was mostly positive but not statistically significant. Thus, the impact of changing climate appeared too weak to overcome other influential factors (eg decline in grazing and intra- and interspecific competition).


High-elevation plant communities in European mountains are often dominated by dwarf pine (Pinus mugo Turra) (Tsaryk et al 2006), which fulfills important functions in preventing soil erosion, increasing water retention, and providing wildlife habitat. In the Western Carpathians, a subalpine belt dominated by homogeneous thickets of dwarf pine well adapted to extreme conditions occurs between 1500 and 1800 m independently of the substrate (Lukáčik 1999). In the past, the distribution of dwarf pine in the Western Carpathians was negatively affected by grazing by sheep and cattle, with dwarf pine communities reduced to approximately 20% of their original extent in areas that were unsuitable for grazing and replaced by alpine meadows elsewhere (Tsaryk et al 2006; Jodłowski 2007).

After World War II, socioeconomic changes in Central Europe left their imprint on the relationship between the environment and society (Burkovský 2006). With the onset of socialism, extensive protected areas with good infrastructure for nature protection were developed (Knorn et al 2012; Mihai et al 2017). After grazing had ceased in protected areas, dwarf pine cover increased to about 40% of its original extent (Tsaryk et al 2006), often because of extensive reforestation (eg Jodłowski 2007) carried out to reduce the risk of erosion and avalanche formation and to increase evapotranspiration (Sokol 1965).

The understanding of growth processes in dwarf pine thickets is important for predicting temporal dynamics and spatial distribution of this vital alpine ecosystem (Wild and Winkler 2008; Palombo et al 2010). Unlike most pine species (eg, Dovč iak et al 2005), spatial spread of dwarf pine depends not only on seed dispersal and germination, seedling survival and growth, competition with other plants, and disturbance regime, but also on its ability to reproduce vegetatively (Wild and Winkler 2008) by forming polycormones (multistemmed clones), which spread horizontally (Vorčák and Jankovič 2009; Treml et al 2010). This occurs most frequently in plant communities formed by Vaccinium myrtillus L., together with Vaccinium vitis-idaea L., Deschampsia cespitosa L., Avenella flexuosa L., Nardus stricta L., and Juncus trifidus, which are usually dominant in subalpine localities in the Western Carpathians (Vorčák and Jankovič 2009; Treml et al 2010). However, the growth and competitive ability of dwarf pine changes significantly with increasing elevation because of changing environmental conditions and declining competition from other woody species (Takahashi and Yoshida 2009).

In addition to cessation of grazing, global climate warming has been suggested as an important factor driving the spread of dwarf pine (Dirnböck et al 2003; Harsch 2009; Treml et al 2010). While Melo (2005) showed an increase in average temperature in Slovakia over the past 50 years maximally by 1.4°C, in the longer time period 1881–2017 there was an increase of 1.73°C with an average decrease in total precipitation of 0.5% (Ministry of Environment 2017). Dwarf pine distribution can be reduced by the expansion of trees colonizing the lower parts of the dwarf pine vegetation belt, but it can expand to higher elevations as climate warming may offset adverse climatic conditions and lengthen the growing season there (Wada et al 2005; Takahashi and Yoshida 2009). Consequently, relic alpine meadows above the dwarf pine belt may be threatened by climate warming and dwarf pine expansion on mountains of lower elevation. Because of their competitive ability, compact cover, and vegetative regeneration, expanding dwarf pine thickets can exert a strong negative influence on the biodiversity of alpine meadows by reducing habitat for heliophytic alpine plants and many insect species (Kuras et al 2001). The dynamics of polycormone spread may, therefore, be one of the most important issues in biodiversity conservation in mountain areas with the occurrence of dwarf pine affected by the changing climate (see Treml et al 2010).

In alpine ecosystems, species growth and distribution are particularly sensitive to changing climatic conditions (Körner 1994; Grabherr et al 2000). A changing growth rate is generally considered to be a valuable indicator of tree response to changing environmental conditions (Bär et al 2006; Wason et al 2017). Trees and shrubs growing above the treeline tend to have a prostrate growth form (Dai et al 2017) with radial growth characterized by frequent occurrence of compressed wood and missing or wedging annual tree rings (Schweingruber 1996; Bär et al 2006). This makes it difficult to measure radial tree growth by tree rings. In dwarf pine, this difficulty can be overcome by focusing instead on annual stem length increments, which are more substantial, regular, and easily detectable due to scars on the bark (Takahashi and Yoshida 2009), as commonly measured in numerous studies (eg Kajimoto 1993; Wada et al 2005; Kyncl 2006; Špinlerová and Martinková 2006; Maděra et al 2011; Lukáčik et al 2014). Combining this approach with photogrammetry using historical and recent aerial images can be a powerful tool for detecting patterns and drivers of changes in the distribution of dwarf pine thickets in mountain landscapes affected by changing climate (eg Mihai et al 2007; Treml et al 2010; Švajda et al 2011; Solár 2013; Solár and Janiga 2013; Dai et al 2017).

In this study, we investigated the spatial dynamics of dwarf pine on 2 mountains in the Orava Beskids section of the Western Carpathians over several decades (from 1949 to 2013). Our main objectives were to quantify and contrast changes in dwarf pine cover in areas of both natural recolonization and reforestation, and to examine if dwarf pine growth and thus distribution may be changing because of changing climate.

Material and methods

Study area

The study was conducted at 2 sites, on the mountains Babia hora and Pilsko, located in the Slovakian portion of the Orava Beskids, a mountain range in the Western Carpathians ( Supplemental material, Figure S1 (mred-38-04-342-352_s01.pdf), Babia hora, with a summit elevation of 1725 m, is the highest peak in the Orava Beskids. Pilsko is a separate massif with a summit elevation of 1557 m. The bedrock of the Orava Beskids is Magura-flysch, and the most frequently represented soil types are podzolic Cambisols, Rankers, and Podzols, while humic Podzols dominate in higher elevations (Lukniš et al 1972). Average annual temperature is 2°C (6°C in the growing season), average annual precipitation is 1600 mm (600700 mm in the growing season), and snow cover lasts on average from October to May (Lukniš et al 1972). The study sites were located above the alpine treeline, where forest composition changes gradually from forests dominated by Norway spruce (Picea abies (L.) H. Karst.) to dwarf pine and juniper (Juniperus communis var. saxatilis Pall.) stands. The plant communities of the area belong to the phytosociological class Loiseleurio-Vaccinieta Eggler ex Schubert 1960, order Rhododendro-Vaccinietalia Br.-Bl. et Jenny 1926, and alliance Vaccinion myrtilli Krajina 1933 (Kliment et al 2007).

Based on historical forest management plans, in Pilsko, the natural spread of dwarf pine was augmented substantially by reforestation carried out in the mid-1970s using a chessboard planting pattern to increase the stability of snow and soil layers; the total planted area was approximately 17 ha in the elevation zone 1450–1550 m and 1.5 ha in the elevation zone <1450 m . (Unfortunately, planting details and maps were not preserved to clearly and consistently separate these plantings from the surrounding natural populations.) Reforestation with dwarf pine did not occur on Babia hora. The study areas are designated National Nature Reserves with the highest degree of protection; no intervention is permitted except for the maintenance of hiking trails.


Main characteristics of aerial imagery used to map dwarf pine distribution.a)


Data collection and analysis

We used digital photogrammetry to analyze spatial distribution and temporal changes in dwarf pine cover, and field measurement of annual stem (length) growth increments to measure dwarf pine growth.

Spatial distribution and temporal changes: To reconstruct dwarf pine cover, we selected and analyzed historical and recent aerial images. A dataset for 1949 was extracted from the Historical Orthophoto Map of Slovakia (2013). Additional datasets were extracted from black-and-white aerial images taken in 1973 and 1992 (Topographic Institute, Banská Bystrica, Slovakia, 2016) and from truecolor digital images taken in 2013 (National Forestry Centre, Zvolen, Slovakia, 2013) (Table 1). The 1949 aerial data for Pilsko were incomplete and were excluded from analysis.

Data processing consisted of 3 levels: digital photogrammetry, image classification, and geographic information systems (GIS) analysis with cartographic representation.

A combination of traditional methods of aerotriangulation and orthorectification (eg Wolf and Dewitt 2000; Mikhail et al 2001) and some specific workflows for archival photogrammetry (eg Prokešová et al 2010) were used to obtain spatially correct orthoimages. The workflow started with interior orientation of the images. Then the exterior orientation for individual images was computed using automatic aerotriangulation with iterative bundle block adjustment, in which leastsquares adjustments were applied to the ground control points (Prokešová et al 2010) in order to obtain the best solution for the triangulation equations. Historical aerial images with computed exterior orientation parameters were orthorectified using the same digital elevation model (5 m grid) generated from the 2013 images with 0.5 m resolution orthoimages.

Object-oriented classification was performed according to the methodology presented in Treml et al (2010), based on the multiresolution segmentation of raster layers and following classification of segments using a combination of nearest neighbor classifier and membership functions resulting in 2 classes: dwarf pine and others. Despite this methodology, a number of manual classifications had to be done to obtain reliable and comparable measures of the area of dwarf pine cover in a given period. The accuracy of automatic objectoriented classification was computed based on the training test area mask ( Supplemental material, Figure S2 (mred-38-04-342-352_s01.pdf),, which served as a correct reference layer containing manually corrected dwarf pine cover for each period. The results of these classifications were analyzed using Cohen's Kappa statistic (Cohen 1960), where values for the kappa index of agreement range from 0 to 1. According to Landis and Koch (1977), values greater than 0.80 represent strong agreement, and values between 0.40 and 0.80 represent moderate agreement.


Dwarf pine expansion on Babia hora (1949–2013) and Pilsko (1973–2013), as delineated from aerial photographs, with the location of the linear transects used in the study and the aerial photographs shown in Figures 2 and 3. (Maps by authors)


Data representing the dwarf pine cover area were analyzed in GIS by study site and elevation zone: <1450 m, 1450–1550 m, and >1550 m. Pilsko's highest elevation is 1557 m, and thus it does not have a >1550 m zone.

Dwarf pine's natural spread over time was evaluated directly from the aerial imagery by analyzing changes in the dimensions (object-oriented classification) of its polycormones over time (1973–2013) as a function of study site, elevation zone, competition from spruce (present versus absent), and direction of spread (following contour lines versus slope). Polycormones were selected for analysis from the aerial images (≥20 polycormones for each elevation zone and competition variant on each site) only when they had clearly identifiable borders that allowed unambiguous delineation of separate polycormones on old and new images. Significant differences in polycormone spread over time were tested using one-way ANOVA with a post-hoc Tukey HSD (Honest Significant Difference) test.

Field measurements: To corroborate the biological basis for the dwarf pine spread quantified from the aerial imagery, we carried out field measurements of annual dwarf pine stem (length) growth increments in June 2017 using visible growth scars on the bark. (Since growth was not completed for 2017 in June, this length increment was not analyzed.) Annual length increments were measured along linear transects following contour lines (1 per elevation zone, totaling 3 transects on Babia hora and 2 on Pilsko; see Figure 1) on 40 stems that intersected the transects (with an accuracy of 1 mm from the stem tip to root collar, excluding 2017 growth). The statistical sample size was determined following Bartlett et al (2001). Mean length increment chronologies were developed for each elevation zone and study site. Polynomial functions were fitted to length increments to assess their trends over time. Goodness of fit was verified through linear regression.


Development of dwarf pine cover by elevation zone and time period on Babia hora and Pilsko. Babia hora is taller than Pilsko and has aerial photography available from 1949, while the first aerial photographs of Pilsko are from 1973.


The homogeneity of length increments was evaluated by the pointer year method, which shows annual growth reactions due to abrupt changes in environmental conditions (especially in climate; Schweingruber 1996). Pointer years (Py) are characterized by reduced (Py ≤_1) or increased (Py ≥1) increments relative to immediately preceding or following years (5-year mowing window). We further analyzed tree growth sensitivity by estimating the annual expression (morphological expression of an event year, Schweingruber 1996) as the percentage of individual stems that were above or below the Py thresholds (≤_1 or ≥1) in any particular year.

To identify climatic factors controlling dwarf pine growth, correlations between mean length increment chronology and mean monthly weather characteristics (temperature and precipitation) were computed using long-term data for the Orava Beskids obtained from the CRU (Climate Research Unit) TS3.21 dataset (0.5×0.58 grid interpolated points) (Harris et al 2014). The correlations were performed using a 17-month window (from April of the previous year to August of the analyzed year) to include climate variation during the period most influential on tree growth (Dirnböck et al 2003; Treml et al 2010).


Spatial distribution and temporal changes in dwarf pine cover

Dwarf pine thickets were restricted to mountain summits, where they covered 67.7 ha (Babia hora) and 90.3 ha (Pilsko) in 2013 (Figure 1). The overall dwarf pine cover increased by 28.6% on Babia hora over 64 years and by 57.1% on Pilsko over 40 years. The expansion rate varied with time, elevation, and site ( Supplemental material, Figure S2 (mred-38-04-342-352_s01.pdf), On Babia hora, the total expansion rate was quite low at lower and middle elevations (zones <1450 m and 1450–1550), and it was considerably higher at high elevations (>1550 m zone), where the total cover more than doubled between 1949 and 2013 (Table 2). On Pilsko, the largest annual expansion occurred in 1973–1992, following (and partly because of) largely successful reforestation with dwarf pine during this period (about 17 ha planted in the 1450–1550 m zone and 1.5 ha in the <1450 m zone). Dwarf pine continued to spread rapidly in 1992–2013, at higher annual rates in middle elevations and lower rates at lower elevations (Table 2).

These patterns of dwarf pine spread over time are well illustrated by aerial photographs. On Babia hora, dwarf pine thickets tended to be compact (continuous) at middle and low elevations, where they co-occurred with spruce and little open alpine grassland was available for colonization, while at high elevations, dwarf pine occurred mainly in small patches scattered within the matrix of alpine meadows (Figure 2). In contrast, dwarf pine thickets on Pilsko were often patchy and surrounded by alpine grassland even at middle and lower elevations in 1973, providing ample space for dwarf pine expansion by 2013 (Figure 3).

At middle and lower elevations, the spatial spread of individual dwarf pine polycormones was significantly affected (decreased) by competition from spruce but not by site or elevation (Table 3). These statistically significant differences in polycormone spread over time with and without spruce competition were confirmed for both elevation zones and both directions of polycormone growth on Pilsko. (On Babia hora, the number of polycormones fulfilling selection criteria was too low for analysis.)

Patterns and controls of dwarf pine growth

Mean annual length increments varied between sites and elevation zones. In general, annual length increments were greater in middle elevations than in high or lower elevations, and they were lower in Pilsko than in Babia hora (Table 3). The mean length increment chronologies of the individual elevation zones further corroborated that growth was generally greater at middle elevations than at high or lower elevations, and that growth at middle elevations appeared to first increase and then decline over time on Babia hora, while temporal trends in other elevations and on Pilsko were less pronounced (Figure 4, left). Despite these differences, the mean length increment chronologies of the individual elevation zones were significantly correlated with each other on both sites (all P < 0.01; Babia hora 0.45, 0.66; Pilsko 0.52), making it possible to average the chronologies of each site (Figure 4, right).


Aerial photographs showing the natural distribution of dwarf pine thickets on Babia hora in 1949 and 2013 by elevation zone. Each photograph represents an area of 4 ha (200 × 200 m). Dwarf pine thickets show as smooth dark grey or dark green patterns; lighter shades of gray or green show alpine grassland vegetation, while larger crowns visible at <1450 and 1450–1550 m belong mainly to Norway spruce (Picea abies).


We identified several pointer years after 1973, characterized by abrupt changes in dwarf pine growth (Babia hora: 12, Pilsko: 14) (Figure 4, right). The majority (80%) of the pointer years were the same for the 2 sites, suggesting that dwarf pine growth varied over time in similar ways at both sites. However, the mean annual expression (mean percentage of stems responding to pointer years positively or negatively) was quite low on both sites (ranging from 13% to 16%), with a significant (exhibited on >50% of trees) annual growth response not occurring at all on Babia hora and occurring only twice on Pilsko (negative in 2014 and positive in 2016) (Figure 4, right).

Due to the similarity of the 2 sites in climate and dwarf pine growth, they were pooled together to investigate the relationship of dwarf pine growth to climate. Statistically significant positive correlations of mean growth chronology and monthly temperature were recorded for the growing season when growth occurred and the preceding growing season (Figure 5). The correlations of mean growth chronology with monthly precipitation were not statistically significant.

Discussion and conclusions

Dwarf pine spread over time in our study varied with elevation as it integrated declining growth and changing inter- and intraspecific competition with elevation, as corroborated by other studies (Takahashi and Yoshida 2009; Vorčák and Jankovič 2009). Our study area (the Orava Beskids) is characterized by the coldest climate in the Western Carpathians, with the upper forest limit almost 100 m lower (at 1350–1450 m above sea level) than on other mountains in the region (Vorčák and Jankovič 2009). This is consistent with the relatively low cover of dwarf pine and the presence of spruce in the <1450 m zone in our study. Spruce can occur at higher elevations on southwestern aspects (as it did in our study), where it vigorously competes with dwarf pine, while dwarf pine can descend to lower elevations in areas where spruce is excluded because of poor substrate or an unfavorable local microclimate (eg talus slopes or terrain depressions with snow accumulation) (Tranquillini 1979; Mihai et al 2007; Carcaillet et al 2009; Treml et al 2010). Despite strong competitive pressure from spruce in the lower elevations, dwarf pine was still able to spread into open areas and substantially increase over time (naturally by 23.6% on Babia hora, and by 38.5% on Pilsko, where natural populations were augmented by plantings).


Aerial photographs showing the distribution of dwarf pine thickets on Pilsko in 1973 and 2013 by elevation zone. Each photograph represents an area of 4 ha (200 × 200 m). The 4 photographs on the left show naturally established thickets, while the 2 photographs on the right show dwarf pine plantings (artificial regeneration), visible as dark green squares on the 2013 photograph. See Figure 2 caption for additional interpretation of the photographs.


Although the largest natural dwarf pine cover on Babia hora was in the middle elevations, dwarf pine expansion in this zone was relatively modest (19.1%), reflecting that much of the area was already colonized by this species (see Pagan and Randuška 1987; Wild and Winkler 2008). The largest increase in dwarf pine cover (>100% over 64 years) occurred at the high elevations, where dwarf pine formed patches scattered within the grassland matrix; studies on other mountains also suggested fast spread rates for scattered dwarf pine polycormones (60% increase over 40 years, Treml et al 2010; the greatest expansion rates in high elevations, Mihai et al 2007). Thus, our study adds evidence that dwarf pine can rapidly expand into alpine meadows as documented elsewhere in Slovakia (eg Švajda et al 2011; Solár 2013; Solár and Janiga 2013) and across Europe (eg Mihai et al 2007; Carcaillet et al 2009; Palombo et al 2010; Dai et al 2017). This dwarf pine expansion is consistent with woody invasions of montane meadows following their abandonment, for example cessation of hay making or grazing (Dovčiak et al 2015), and with upward vegetation shifts induced by climate warming (Harsch et al 2009). As the climate has become warmer (by 0.7 to 1.4°C) and drier at high elevations in Slovakia over the past 50 years (Melo 2005), our study lends some support to the climate change hypothesis (dwarf pine growth was positively related to temperature) but more to the land-use change hypothesis (dwarf pine growth did not continue to increase consistently over time with warming).


Dwarf pine growth over time: length increment of stems and spread of polycormone by study site, elevation zone, and presence of spruce competition (mean ± SD). Letters indicate statistically significant (P < 0.05) differences.



Mean length increment chronologies per elevation zone (left) and their site means with annual expressions and pointer years (Py) (right) for Babia hora and Pilsko. Polynomial fits are shown only as an aid in interpreting the graphs (goodness of fit expressed by R 2 = 0.2–0.5). Py were not evaluated when sample size dropped below 5 individuals. Annual expression was measured as the percentage of stems with positive or negative growth responses in any particular year.


In contrast to the natural spread on Babia hora, dwarf pine spread on Pilsko was augmented by chessboard plantings that substantially increased its cover during 1973–1992 and facilitated continuing species expansion in the post-planting 1992–2013 period. Thus, reforestation by dwarf pine appears to be a viable management strategy for avalanche and soil erosion control in mountain areas where forest cover has been reduced by grazing or other disturbance (see García-Hernández et al 2017). The high rate of expansion in the middle elevations on Pilsko (nearly 70% over 40 years) contrasted with much slower expansion from the natural populations on Babia hora in this elevation zone (about 19% over 64 years), suggesting that the chessboard planting pattern allowed rapid expansion from planted patches into the open spaces among them, similar to the expansion occurring from the scattered dwarf pine patches at the high elevations on Babia hora (>100% over 64 years). Both the checkerboard plantings on Pilsko and the naturally patchy distributions of dwarf pine on Babia hora provide support for the efficacy of cluster plantings in the reforestation of high mountain ecosystems (Schönenberger 2001).


Correlations between mean growth chronology and mean monthly temperature and precipitation for 1974–2013. Correlations were calculated using a 17-month window from April of the previous growing season to August of the year when the growth occurred. Months of the previous growing season are marked with P. Asterisks indicate statistically significant correlations (P < 0.05).


Dwarf pine spread over time can be strongly affected by nearby vegetation (Dirnböck et al 2003); it can be particularly successful in communities dominated by the low shrubs (eg Vaccinium myrtillus and Vaccinium vitis-idaea) and grasses (eg Avenella flexuosa and Festuca airoides) (Treml and Šenfelder 2007) that formed communities in our study (phytosociological class Loiseleurio-Vaccinieta; Kliment et al 2007). These communities occur often in higher elevations, and they may potentially facilitate upward spread of dwarf pine as the climate continues to warm. On the other hand, in lower and middle elevations, spruce appeared to negatively affect the spread of dwarf pine polycormones, likely because of competition for light (Jeník and Lokvenc 1962; Treml et al 2010). As warmer climate is expected to shift the treeline and spruce distribution upward, the negative effects of spruce on dwarf pine are likely to intensify and cause the eventual decline of dwarf pine at the margins of its lower elevational range.

Dwarf pine growth varied somewhat between the 2 mountains in our study. This was likely because of edaphic, microclimatic, or vegetation factors (see Takahashi and Yoshida 2009; Lukáč ik et al 2014), since the 2 mountains had a similar regional climate. The mean annual length increments in our study (Babia hora: 7.43– 9.32 cm/yr; Pilsko: 6.78–8.47 cm/yr) were similar to growth reported elsewhere in Central Europe (6.4–8.6 cm, Maděra et al 2011; about 8 cm, Kyncl 2006). However, growth clearly varied across elevations; it was the largest in middle elevations and decreased in high elevations (where climate became more adverse; see Takahashi and Yoshida 2009) and in lower elevations (where competition from spruce increased). The 1450–1550 m zone appeared to be an optimum elevation for dwarf pine growth in the long term, but the growth in natural populations on Babia hora decreased in this zone over the last 2 decades (after reaching the highest values in the 1980s and mid-1990s), probably as a consequence of increasing intraspecific competition. At high and lower elevations where dwarf pine cover was lower, growth trends were less clear, but they appeared to exhibit a weak upward trend consistent with positive climate warming effects on growth (see Pinus pumila growth in Japan; Wada et al 2005).

The lower growth sensitivity to climate was confirmed in our study by annual expressions (only 13–16% of individuals responded to climate on average), while the 2 years with significant growth responses (both on Pilsko) were not related to temperature or precipitation. Growth may reflect other climatic or environmental factors (eg snow cover duration, Dirnböck et al 2003; insect pests, Lukáčik et al 2014). Yet growth in our study did respond positively to temperature, as suggested by the correlations of our length increment chronology with monthly climate variables (particularly with temperature means for April– August and the previous growing season), corroborating similar findings by Dai et al (2017). Temperature and precipitation were closely related to various dwarf pine life stages: the onset of photosynthesis and wood formation in April–May and maximum cell production in June–July (Büntgen et al 2007), and the maturation of needles, shoots, and buds in late summer and autumn (Dirnböck et al 2003; Treml et al 2010; Dai et al 2017). While our study provides moderate evidence that changing climate may have partially driven dwarf pine expansion in the Orava Beskids, other factors (particularly decline in grazing) may have been more important in facilitating the rapid spread of dwarf pine across all elevation belts.


This research was funded by the Slovak Grant Agency for Science (VEGA, project no. 1/0021/18).



Bär A, Bräuning A, Löffler J. 2006. Dendroecology of dwarf shrubs in the high mountains of Norway: A methodological approach. Dendrochronologia 24:17– 27. Google Scholar


Bartlett JE, Kotrlik JW, Higgins CC. 2001. Organizational research: Determining appropriate sample size in survey research. Information Technology, Learning, and Performance Journal 19(1):43–50. Google Scholar


Büntgen U, Frank DC, Kaczka RJ, Verstege A, Zwijacz-Kozica T, Esper J. 2007. Growth responses to climate in a multi-species tree-ring network in the Western Carpathian Tatra Mountains, Poland and Slovakia. Tree Physiology 27(5):689–702. Google Scholar


Burkovský J. 2006. Nature protection in Slovakia in the swirl of development changes. Životné Prostredie 40(5):247–253. Google Scholar


Carcaillet C, Fauvart N, Roiron P, Terral JF, Ali AA. 2009. A new, isolated and endangered relict population of dwarf pine (Pinus mugo Turra) in the northwestern Alps. Comptes Rendus Biologies 332(5):456–463. Scholar


Cohen J. 1960. A coefficient of agreement for nominal scales. Educational and Psychological Measurement 20(1):37–46. Google Scholar


Dai L, Palombo C, Gils H, Rossiter DG, Tognetti R, Luo G. 2017. Pinus mugo krummholz dynamics during concomitant change in pastoralism and climate in the Central Apennines. Mountain Research and Development 37(1):75–86. Google Scholar


Dirnböck T, Dullinger S, Grabherr G. 2003. A regional impact assessment of climate and land-use change on alpine vegetation. Journal of Biogeography 30(3):401–417. Google Scholar


Dovčiak M, Frelich LE, Reich PB. 2005. Pathways in old–field succession to white pine: Seed rain, shade, and climate effects. Ecological Monographs 75:363–378. Google Scholar


Dovčiak M, Hrivnák R, Ujházy K, Gömöry D. 2015. Patterns of grassland invasions by trees: Insights from demographic and genetic spatial analyses. Journal of Plant Ecology 8:46–479. Google Scholar


García-Hernández C, Ruiz-Fernández J, Sánchez-Posada C, Pereira S, Oliva M, Vieira G. 2017. Reforestation and land use change as drivers for a decrease of avalanche damage in mid-latitude mountains (NW Spain). Global and Planetary Change 153:35–50. Google Scholar


Grabherr G, Gottfried M, Pauli H. 2000. GLORIA: A global observation research initiative in alpine environments. Mountain Research and Development 20(2):190–191. Google Scholar


Harris I, Jones PD, Osborn TJ, Lister DH. 2014. Updated high-resolution grids of monthly climatic observations: The CRU TS3.10 dataset. International Journal of Climatology 4:623–642. Google Scholar


Harsch MA, Hulme PE, McGlone MS, Duncan RP. 2009. Are treelines advancing? A global metaanalysis of treeline response to climate warming. Ecology Letters 12:1040–1049. Google Scholar


Historical Orthophotomap of Slovakia. 2013. Geodis Slovakia, s.r.o.; accessed on 8 June 2018. Google Scholar


Jeník J, Lokvenc T. 1962. Alpine Treeline in the Krkonoše Mountains [in German]. Rozpravy Č SAV, ser. Math.—Nature, Prague, Czech Republic: Czechoslovak Academy of Sciences. Google Scholar


Jodłowski M. 2007. Krummholz-Line in the Tatra Mts. Babia Góra and the Giant Mts. Ecotone Structure and Dynamics [in Polish] [PhD dissertation]. Kraków, Poland: Institute of Geography and Spatial Management of the Jagiellonian University. Google Scholar


Kajimoto T. 1993. Shoot dynamics of Pinus pumila in relation to altitudinal and wind exposure gradients on the Kiso mountain range, central Japan. Tree Physiology 13:41–53. Google Scholar


Kliment J, Valachovič M, Bernátová D, Dúbravcová Z, Jarolímek I, Petrík A, Šibík J, Uhlířová J. 2007. Rastlinné spoločenstvá Slovenska 4. Vysokohorská vegetácia. Bratislava, Slovakia: Veda. Google Scholar


Knorn J, Kuemmerle T, Radeloff VC, Szabo A, Mindrescu M, Keeton WS, Abrudan I, Griffiths P, Gancz V, Hostert P. 2012. Forest restitution and protected area effectiveness in post-socialist Romania. Biological Conservation 146:204–212. Google Scholar


Körner C. 1994. Impact of atmospheric changes on high mountain vegetation. In : Benniston M, editor. Mountain Environments in Changing Climates. London, United Kingdom: Routledge, pp 155–166. Google Scholar


Kuras T, Beneš J, Konvička M. 2001. Behaviour and within-habitat distribution of adult Erebia sudetica sudetica, endemic of the Hruby Jeseník mts., Czech Republic (Nymphalidae, Satyrinae). Nota Lepidopterologica 24:69–83. Google Scholar


Kyncl T. 2006. Growth rate evaluation of dwarfpine [in Czech]. In : Hošek J, editor. Vliv výsadeb borovice kleče (Pinus mugo) na biotopovou a druhovou diverzitu arkto-alpinské tundry ve Východních Sudetech (CHKO Jeseníky, NPR Králický Sněžník). Návrh managementu těchto porostů. Prague, Czech Republic: Ministry of Environment, pp 59–61. Google Scholar


Landis J, Koch G. 1977. The measurement of observer agreement for categorical data. Biometrics 33:159–174. Google Scholar


Lukáčik I. 1999. Growth, reproduction, health status and functional efficiency of mountain pine in the Tatra Mountains. [in Slovak]. In : Kantor P, editor. Pěstovanílesů v podmínkach antropicky zmeneného prostředí. Mendelova zemědělská a lesnická univerzita v Brně. Brno, Czech Republic: Publishing Center of Mendel University in Brno, pp 23–26. Google Scholar


Lukáčik I, Bugala M, Balanda M. 2014. Dendrochronological analysis of the dwarf-pine (Pinus mugo Turra) growth in the High Tatras. Acta Pruhoniciana 106:5–9. Google Scholar


Lukniš M, Bako J, Berta J, Ferianc O, Feriancová-Masárová Z, Fusán O, Futák J, Hejný S, Jurko A, Korbel L, Kurpelová M, Mičian Ľ, Michalko J, Petrovič Š, Schmidt Z, et al. 1972. Slovakia 2—Nature [in Slovak]. Bratislava, Slovakia: Obzor. Google Scholar


Maděra P, Buček A, Culek M, Friedl M, Kirchner K, Pecháček J, Roštínsky P, Sedláček A, Šenfedlr M, Špinlerová Z, Štykar J, Tippner A, Vavříček D. 2011. Geobiocenoses of the Upper Treeline, Influence of the Dwarf Pine Vegetation on the Mountain Landscape in Hrubý Jeseník Mountains, and Risks Associated with Its Removal [in Czech]. Brno, Czech Republic: Publishing Center of Mendel University in Brno. Google Scholar


Melo M. 2005. Warmer periods in the Slovak mountains according to analogue method and coupled GCM. Croatian Meteorological Journal 40:589– 592. Google Scholar


Mihai B, Săvulescu I, Rujoiu-Mare M, Nistor N. 2017. Recent forest cover changes (2002–2015) in the Southern Carpathians: A case study of the Iezer Mountains, Romania. Science of the Total Environment 599–600:2166–2174. Google Scholar


Mihai B, Savulescu I, Sandric I. 2007. Change detection analysis 1986–2002 of vegetation cover in Romania. Mountain Research and Development 27(3):250–258. Google Scholar


Mikhail EM, Bethel JS, McGlone JC. 2001. Introduction to Modern Photogrammetry. New York, NY: John Wiley & Sons. Google Scholar


Ministry of Environment of the Slovak Republic. 2017. The Seventh National Communication of the Slovak Republic on Climate Change [in Slovak]. Bratislava.; accessed on 19 September 2018. Google Scholar


Pagan J, Randuška D. 1987. Atlas of tree species 1. Bratislava, Slovakia: Obzor. Google Scholar


Palombo C, Lasen C, Sciré M, Garfì V, Lombardi F, Tognetti R, Marchetti M. 2010. Structural and dendrochronological characterization of mountain pine persistent woodlands on the Monti del Sole: Dolomiti Bellunesi National Park. L'Italia Forestale e Montana 6:737–749. Google Scholar


Prokešová R, Kardoš M, Medveďvá A. 2010. Landslide dynamics from highresolution aerial photographs: A case study from the Western Carpathians, Slovakia. Geomorphology 115(1–2):90–101. Google Scholar


Schönenberger W. 2001. Cluster afforestation for creating diverse mountain forest structures: A review. Forest Ecology and Management 145(1–2):121– 128. Google Scholar


Schweingruber FH. 1996. Tree Rings and Environment: Dendroecology. Bern, Switzerland: Paul Haupt. Google Scholar


Sokol F. 1965. The Influence of the Natural Environment and Human Activity on the Formation of Landslides and Experience with Their Recultivation in Hrubý Jeseník Mountains. [in Czech] [PhD dissertation]. Brno, Czech: Publishing Center of Mendel University in Brno. Google Scholar


Solár J. 2013. Effect of climate change on mountain pine distribution in western Tatra Mountains. In : Singh BR, editor. Climate Change: Realities, Impacts Over Ice Cap, Sea Level and Risks. Rijeka, Croatia: InTech, pp 437–458. Scholar


Solár J, Janiga M. 2013. Long-term changes in dwarf pine (Pinus mugo) cover in the High Tatra Mountains, Slovakia. Mountain Research and Development 33(1):1–61. Scholar


Špinlerová Z, Martinková M. 2006. Growth of mountain pine (Pinus mugo Turra) in relation to the use of other tree species. Journal of Forest Science 52(5):217–225. Google Scholar


Švajda J, Solár J, Janiga M, Buliak M. 2011. Dwarf pine Pinus mugo and selected abiotic habitat conditions in the western Tatra Mountains. Mountain Research and Development 31(3):220–228. Google Scholar


Takahashi K, Yoshida S. 2009. How the scrub height of dwarf pine Pinus pumila decreases at the treeline. Ecological Research 24:847–854. Google Scholar


Tranquillini W. 1979. Physiological Ecology of the Alpine Timberline. Berlin, Germany: Springer. Google Scholar


Treml V, Šenfelder M. 2007. Generative spreading of dwarf pine on localities Keprník and Větrná louka in Hrubý Jeseník mts. [in Czech]. In : Hošek J, editor. Vliv výsadeb borovice kleče (Pinus mugo) na biotopovou a druhovou diverzitu arkto-alpinské tundry ve Východních Sudetech (CHKO Jeseníky, NPR Králický Sněžník). Návrh managementu těchto porostů. Prag, Czech Republic: Ministry of Environment, pp 121–140. Google Scholar


Treml V, Wild J, Chuman T, Potůčková M. 2010. Assessing the change in cover of non-indigenous dwarf-pine using aerial photographs, a case study from the Hrubý Jeseník mts., the Sudetes. Journal of Landscape Ecology 4(2):90–104. Google Scholar


Tsaryk I, Didukh YP, Tasenkevich L, Waldon B, Boratyński A. 2006. Pinus mugo Turra (Pinaceae) in the Ukrainian Carpathians. Dendrobiology 55:39–49. Google Scholar


Vorčák J, Jankovič J. 2009. Propagation of spruce at timberline of supramontane degree and in subalpine degree of Babia hora and Pilsko in the Orava Beskids. Forestry Journal 55(1):29–46. Google Scholar


Wada N, Watanuki K, Narita K, Suzuki S, Kudo G, Kume A. 2005. Climate change and shoot elongation of Alpine dwarf pine (Pinus pumila Regel): Comparison between six Japanese mountains. Phyton (Austria) 45:253–260. Google Scholar


Wason JW, Dovciak M, Beier CM, Battles JJ. 2017. Tree growth is more sensitive than species distributions to recent changes in climate and acidic deposition in the northeastern United States. Journal of Applied Ecology 54:1648–1657. Google Scholar


Wild J, Winkler E. 2008. Krummholz and grassland coexistence above the forestline in the Krkonoše Mountains: Grid-based model of shrub dynamics. Ecological Modelling 213:293–307. Google Scholar


Wolf PR, Dewitt BA. 2000. Elements of Photogrammetry with Applications in GIS. Boston, MA: McGraw-Hill. Google Scholar


Supplemental material

FIGURE S1 Location of study sites (Babia hora: 49.573050, 19.529548; Pilsko: 49.528001, 19.316791). (Map by authors)

FIGURE S2 Dwarf pine cover evaluated from aerial imagery in individual years and confusion matrixes based on training test area masks. (Maps by authors)

Found at DOI: 10.1659/MRD-JOURNAL-D-18-00049.S1 (846 KB PDF).

© 2018 Parobeková et al. This open access article is licensed under a Creative Commons Attribution 4.0 International License ( Please credit the authors and the full source.
Zuzana Parobeková, Michal Bugala, Miroslav Kardoš, Martin Dovciak, Ivan Lukáčik, and Milan Saniga "Long-Term Changes in Dwarf Pine (Pinus mugo Turra) Cover and Growth in the Orava Beskid Mountains, Slovakia," Mountain Research and Development 38(4), 342-352, (1 November 2018).
Received: 1 September 2018; Accepted: 1 October 2018; Published: 1 November 2018

alpine treeline
archival photogrammetry
climate change
growth sensitivity
length increment
Species spread
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