Next Article in Journal
Sustainable Livestock Production in Nepal: A Focus on Animal Nutrition Strategies
Next Article in Special Issue
Agroforestry Extent in the United States: A Review of National Datasets and Inventory Efforts
Previous Article in Journal
Analysing Farmers’ Herbicide Use Pattern to Estimate the Magnitude and Field-Economic Value of Crop Diversification
Previous Article in Special Issue
Comparative Water Environment Simulation Study of Two Typical Models with BMPs in a Karst Basin
 
 
Font Type:
Arial Georgia Verdana
Font Size:
Aa Aa Aa
Line Spacing:
Column Width:
Background:
Communication

Abandonment of Silvopastoral Practices Affects the Use of Habitats by the European Hare (Lepus europaeus)

Forest Research Institute, Hellenic Agricultural Organization DIMITRA, 570 06 Thessaloniki, Greece
*
Author to whom correspondence should be addressed.
Agriculture 2022, 12(5), 678; https://doi.org/10.3390/agriculture12050678
Submission received: 30 March 2022 / Revised: 8 May 2022 / Accepted: 9 May 2022 / Published: 10 May 2022
(This article belongs to the Special Issue Agroforestry Planning)

Abstract

:
Silvopasture, a traditional agroforestry practice, combines the presence of trees, shrubs, herbage, and livestock in time and space to provide multiple ecosystem services that contribute to human well-being. However, the abandonment of traditional agroforestry practices across Europe has led to substantial changes in vegetation characteristics, mainly due to woody plant expansion and, as a consequence, changes in wildlife that rely on open habitats. This study examines the effects of a 20-year abandonment of silvopastoral practices (i.e., livestock grazing and fuelwood harvesting) in a typical agroforestry Mediterranean landscape (kermes oak shrubland, natural grassland, and olive groves) on European hare (Lepus europaeus) habitat use. We estimated tree, shrub, and herb cover using a densitometer and hare habitat use using pellet counts within 2004-m2 rectangular plots in 2002, 2011, and 2021. Hare pellet density in olive groves was significantly lower in 2021 compared to 2002, while the opposite trend was found in grassland for the same period. Woody plant cover expanded from 2002 to 2021. We suggest that the woody plant encroachment that followed the abandonment of traditional silvopastoral practices in the area is the main driver behind the reported decline in hare use of the habitat, as it became less open and therefore less favorable for the species. Maintaining a mosaic of open and closed habitats at the landscape level, which was once provided by silvopastures, is vital for the conservation of this species.

1. Introduction

Silvopasture is among the oldest traditional agroforestry practices; it combines the presence of trees, shrubs, herbage and livestock in the same time and space [1,2]. It has been practiced since the Neolithic times [3], creating landscapes with high habitat heterogeneity including wooded, open, partially open, and shrubland areas [2,4]. These silvopastoral systems, under appropriate management, can lead to more effective and sustainable land use in relation to other single land use systems [5], providing multiple ecosystem services, such as erosion control, fire prevention, biodiversity enhancement, and carbon storage, that contribute to human well-being [6,7]. As a result, appropriate design and implementation of silvopastoral systems can maximize both environmental benefits and livestock productivity, and silvopasture should therefore be recognized as an efficient use of agricultural land.
Despite their recognized value in terms of environmental and human well-being, silvopasture and other agroforestry systems have been gradually abandoned across Europe over the last decades due to a series of environmental and socio-economic factors [4,8]. Although the reasons behind these landscape level changes are complex, agricultural land abandonment in some areas and agricultural intensification in others have been identified as the major drivers [9,10,11,12]. Agroforestry abandonment has been recorded during the last decades throughout Europe [4,11], resulting in more homogenized landscapes and changes in their floral and faunal communities [12]. One species that has been negatively affected by the observed landscape homogenization in once agroforestry landscapes is the European hare (Lepus europaeus Pallas—hereafter hare), the populations of which typically thrive in habitats with high heterogeneity [13,14].
The European hare has a wide range across Eurasia and has been successfully introduced into other countries around the globe [15,16]. However, declines in its population size have been reported in many areas since the 1960s [16,17]. These have been associated mainly with the intensification of agricultural practices, land cover changes, diseases, and pollutants [16,18,19]. The hare prefers grazed and partially disturbed habitats, such as grasslands, scrublands, clearings in scrub and forest stands, and farmland [20,21], and this is why habitat heterogeneity plays a key role in its population dynamics [13,14,16,17,22]. Although its diet consists of a wide range of herb species, grasses and graminoids usually constitute the bulk of its diet composition [23,24].
Livestock grazing, as well as other anthropogenic activities such as tree and shrub growing for fruits, firewood, fodder for animals, etc., affect the composition, structure and the secondary succession of vegetation, which is often beneficial for wild herbivores predominating in areas at early vegetation succession stages [18,19]. Grazing regimes in silvopastoral areas, along with the other human activities associated with tree and shrub exploitation, can influence plant communities in ways that usually promote habitat heterogeneity [25,26]. For example, hares use moderately grazed pastures (about 40% of the annual production grazed) with a sparse herb layer more intensively than lightly grazed pastures (about 20%), and avoid ungrazed patches [27]. Furthermore, grazing reduces vegetation height, which is thought to be advantageous for small- and medium-sized herbivores such as the hare, as they can visually better detect predators [27,28,29]. Similar effects of livestock grazing on vegetation and wildlife by retarding vegetation succession and maintaining a low vegetation height have also been reported on the northwestern European coast [30,31]. Therefore, silvopastoral practices can be a valuable ‘tool’ for managers aiming to improve small- and medium-sized herbivore habitats [27,32]. Despite its importance, little is known about the long-term impact on wildlife’s use of abandoned silvopastures.
The aim of this study was to investigate the effects of silvopastoralism abandonment in a typical Mediterranean system on habitat use by the hare. Although agroforestry systems (including silvopastoral ones) have been reported as rich in biodiversity, the majority of relevant studies focus on birds, plants, fungi, and insect assemblages [33]. To our knowledge, this is the first study reporting on hare habitat use changes over a 20-year period since silvopastoralism abandonment. Our null hypothesis was that there would be no significant difference in the use of olive farms, kermes oak shrubland, and permanent grassland by the European hare after silvopastoral abandonment in a typical Mediterranean landscape. Given that the hare is known to avoid ungrazed sites [27] and uses microhabitats covered by short and sparse herb layer [34], we predicted that the null hypothesis would be rejected by our results.

2. Material and Methods

2.1. Study Area Description

The study was conducted in a 190 ha area (38°43′27.9″–38°42′31.2″ Ν, 22°33′22.2″–22°34′23.7″ Ε, elevation 520–900 m) located in central Greece (Figure 1). This area consists of a mosaic of kermes oak (Quercus coccifera L.) shrubland (approximately 55%), permanent grassland (about 35%), and olive groves (about 10%). We considered these three habitat categories (i.e., kermes oak shrubland, grassland, olive groves) as treatments. The soil is shallow, of low productivity, and partially degraded. The climate is semiarid with cold winters and hot dry summers. Mean annual temperature was 15.7 ± 0.43 °C and mean annual precipitation 966.3 ± 240.75 mm during the period 2006–2021. Meteorological data were derived from the nearest meteorological station (7.5 km south of the study area, elevation 440 m).
Kermes oak shrubland occupies the largest part of the study area. Livestock grazing was the primary land use in the area and the shrubland has also been exploited for firewood for many years. The shrub layer, in addition to the dominant kermes oak, also includes prickly juniper (Juniperus oxycedrus L.), Jerusalem thorn (Paliurus spina-cristi Mill.), hawthorn (Crataegus monogyna Jacq.), mastic tree (Pistacia lentiscus L.), Rosa spp., Mediterranean buckthorn (Rhamnus alaternus L.), and almond-leaved pear (Pyrus spinosa Forssk.). Phryganic plants also occur in this shrubland, with the main species being Thymus spp., thorny burnet (Sarcopoterium spinosum Spach.), asparagus (Asparagus acutifolius L.), and Cistus spp., whereas the most important herb species are goatgrass (Aegilops triuncialis L.), cocksfoot (Dactylis glomerata L.), and squarrose brome (Bromus squarosus L.).
Grasslands are dominated by goatgrass, cocksfoot, squarrose brome, drooping brome (Bromus tectorum L.), mosquito grass (Dasypyrum vilosum L.), cocksfoot, Lathyrus spp., Vicia spp., Trifolium spp., and Ranunculus spp. Sparse trees, shrubs, and phryganic plants also occur such as almond-leaved pear, kermes oak, Jerusalem thorn, and asparagus.
Olive groves are cultivated in the study area primarily for olive oil production and secondarily for table olives. The layer of trees (overstory) is dominated by olive trees and the layer of herbs (understory) by goatgrass, cocksfoot, squarrose brome, drooping brome, species of the Asteraceae family, etc. The shrub layer is practically absent, with only few individuals of kermes oak, Jerusalem thorn, and Rubus spp. usually growing solitarily near the trunks of the olive trees.
The entire study area was grazed by mixed sheep and goat herds (approximate ratio 4:1) for several decades, following a traditional continuous grazing system. However, the number of livestock grazing in the study area gradually reduced from 350 to 100 animals from 1985 to 2000, and since 2002, no livestock grazing has occurred, as people moved to urban centers and pastoral life was abandoned. At that time (2002), about 80–90 residents were living in the nearest village (Drymaia) with about 90% of them aged over 65. The same trend of pastoralism has been observed for the other silvopastoral practices in the area, such as olive cultivation and firewood collection.

2.2. Plant Cover

In each treatment (kermes oak shrubland, grassland, olive groves), three transects (200 m each) were established at the end of spring 2002 (Figure 1), ensuring that transects did not cross vegetation (treatment) boundaries and that they were spaced at least 80 m apart. We took note of both starting coordinates and directions for all transects. Relative cover of the tree, shrub, and herb layers in each treatment was estimated using a densitometer (GRS™) and the line-point transect method. Measurements were taken every 2 m (100 points per transect) and the measurements were repeated in 2011 and 2020 at the end of spring. The starting point of each transect was located using a handheld global positioning system. Overstory and understory vegetation coverage was recorded by turning the densitometer’s front towards the canopy or to the ground, respectively, while always keeping the densitometer’s body parallel to the ground.

2.3. Pellet Counts

The use of the study area by hares was based on pellet counts, which is to considered to be an appropriate method for estimating the abundance and feeding intensity of hare in an area [35]. We counted hare pellets within ten circular plots with 0.5 m radius per transect (spaced 20 m apart) at the same time and during the same years as the plant cover measurements. The first plot was established at the start of each transect. In total, 30 plots were counted per habitat each year. Special attention was given during plot establishment so as to avoid edge effects. During the experiment, we excluded plots covered with fallen branches, rolling rocks, and other objects to avoid distorting our data. Only fresh pellets (moist, not crumbly, and brown to dark colored) were counted.

2.4. Statistical Analysis

Pellet-count data were subjected to a two-way factorial ANOVA using the SPSS statistical software (version 20.0 Inc., Chicago, IL, USA). Treatments and years were considered as fixed factors. Levene’s test was performed prior to the analysis in order to check the homogeneity of variances. Mean differences were evaluated with Tukey’s honestly significant difference (HSD) test. In order to identify treatments used more often by hares each year, we used a main-effects analysis using SPSS Syntax. Differences were considered significant at p < 0.05.

3. Results

3.1. Plant Cover per Treatment

Tree and shrub coverage increased in all treatments during the 20-year study period. Specifically, tree coverage increased by approximately 6%, 2%, and 10% in shrubland, grassland, and olive groves, respectively, from 2002 to 2021 (Figure 2). A similar increasing trend was observed for shrub coverage, with an 8%, 9%, and 9% increment in shrubland, grassland, and olive groves, respectively. On the contrary, herb coverage was reduced by about 9%, 6%, and 11% in shrubland, grassland, and olive groves, respectively (Figure 2).

3.2. Habitat Use by Hare

Two-way factorial analysis revealed a significant effect of habitat type on the mean number of hare pellets (Table 1), whereas year did not have a significant effect. However, there was a statistically significant interaction (F = 2.683, df = 4, p = 0.032) between habitat and year on the mean number of hare pellets. Simple main effects analysis (pairwise comparisons) showed that the mean number of hare pellets in olive groves was significantly higher (p = 0.031) in 2002 compared to 2021 (Figure 3). In contrast, the mean number of hare pellets in grassland was significantly higher (p = 0.024) in 2021 compared to 2002. No significant differences were found in the mean number of hare pellets in shrubland across years, with it remaining the lowest (ranging from 1.07 pellets/m2 in 2002 to 0.60 pellets/m2 in 2021) throughout the study period. The mean number of hare pellets in the entire study area remained more or less stable (p = 0.915) during the 20-year study period, i.e., 1.99, 2.01 and 2.12 pellets/m2 in 2002, 2011, and 2021, respectively.

4. Discussion

The silvopastoral abandonment in our study area, which commenced in 2002, has initiated secondary succession processes with the encroachment of woody species (trees and shrubs) at the expense of herbs. This can be attributed to the cessation of both livestock grazing and practices associated with silvopastoralism, such as pruning of olive trees and collection of kermes oak for firewood that took place historically in the area. The observed vegetation changes were anticipated and have been documented in abandoned agroforestry systems throughout Europe, especially in the Mediterranean zone [36,37]. The depopulation of rural areas and agricultural intensification during the second half of the 20th century, along with the associated vegetation changes, are expected to negatively affect wildlife species that prefer habitats in earlier stages of succession, such as the hare [16,27].
This was corroborated by the observed higher pellet counts in olive groves in 2002 compared to 2021, whereas grassland use by the hare went in the opposite direction; i.e., grassland use was significantly higher in 2021 than in 2002. It is well known that herbivory and other silvopastoral practices have a prominent role in determining the structure of plant communities [38,39,40,41,42]. It seems that the hare more often uses areas covered by short and sparse vegetation [34]; a behavior thought to be linked to increased hare ability to visually detect approaching predators in such habitats [27,28,29]. However, this behavior may change, at least temporarily, in the case of elevated predation risk [43]. Of course, changes in habitat use could reflect changes in the overall population size of a species [44]. However, in this study, the non-significant differences in the mean number of hare pellets in the entire study area indicates a stability of hare population size during the study period; i.e., the 20-year abandonment of silvopastoral practices seemingly did not negatively affect the hare’s population dynamics. We can therefore reasonably assume that the observed shift in habitat use by hares is probably due to the vegetation changes caused by the abandonment of traditional silvopastoral practices and not by marked changes of its population size. Theoretically, if the observed encroachment of woody species continues during the next decades, then a reduction of the total grassland area is expected to take place and hares may be forced to move out of the study area to look for more preferred feeding areas.
The observed higher use of grasslands by hares in relation to shrublands have been reported in other studies as well [27,28]. However, the low use of kermes oak stands does not mean that this kind of habitat is invalid for hares. It is well documented that such stands, as well as forested areas, provide shelter for adult hares and their offspring against predators [28,45]. In essence, kermes oak stands may be of trivial importance as feeding places for hares, but they may be of prime importance for their survival ability and reproduction success.
Our findings show the hare’s ability to adapt to vegetation cover changes in an area by shifting habitat use. Such behavioral plasticity in the face of environmental changes has been previously reported for the species [45,46]. Although the study design (monitoring of three years spaced along a 20-year interval) was not able to capture nuanced changes and interannual variation in habitat structure, we believe that it is adequate for the aim of this study, i.e., to investigate the long-term effects of silvopastoralism abandonment on the use of olive farms, kermes oak shrubland, and permanent grassland by the hare in a typical Mediterranean system. However, along with the changes of coverage of main plant forms (tree, shrub, herbage) investigated in this study, other vegetation characteristics have also been reported to influence the use of space by hares. For example, sparse and low-height vegetation communities in grasslands are used more intensively by hares in relation to dense and tall herbage communities [27]. In addition, the movement behavior of hares can be influenced by the presence of specific plant species [46,47]. For vulnerable species such as the hare, the availabilities of both forage and cover (shelter against predators) have been reported as critical factors affecting the use of space [28,48]. From this perspective, the presence of the specific plant species that constitute the bulk of the diet of the hare and/or provide shelter against predators could influence the spatial distribution of the hare in this study. Future research should focus on further understanding the effect of traditional silvopastoral practices on modifying vegetation structure and composition in relation to hare population dynamics and behavior.

5. Conclusions

In our study area, Silvopastoral abandonment since 2002 (cessation of livestock grazing, olive cultivation, firewood collection) initiated secondary succession processes that provided the opportunity for the encroachment of woody species (trees and shrubs) at the expense of herbs. These vegetative changes had cascading effects on hare habitat use patterns, as this species prefers habitats in earlier stages of vegetation succession. The lower use of olive groves by the hare, which was accompanied by increased use of grasslands, shows the species’ aversion to the vegetation structure changes that occurred following silvopasture abandonment. The habitat use plasticity of the hare to landscape level vegetation changes suggests that silvopastoralism, under appropriate management, can be used as a “tool” for the conservation of hare populations.

Author Contributions

Conceptualization, I.K.; methodology, I.K.; software, I.K.; formal analysis I.K. and D.F.; investigation, I.K.; writing—original draft preparation, I.K.; writing—review and editing, I.K., T.G.P. and D.F.; supervision, T.G.P. All authors have read and agreed to the published version of the manuscript.

Funding

This research was partially funded by the Research Committee of University of Thessaly (former TEI of Thessaly).

Institutional Review Board Statement

Not applicable.

Informed Consent Statement

Not applicable.

Data Availability Statement

Publicly available datasets (climatological data) were analyzed in this study. This data can be found here: (https://penteli.meteo.gr/stations/amfiklia/, accessed on 29 March 2022).

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. Blondel, J. The ‘Design’ of Mediterranean Landscapes: A Millennial Story of Humans and Ecological Systems during the Historic Period. Hum. Ecol. 2006, 34, 713–729. [Google Scholar] [CrossRef]
  2. Ferraz-de-Oliveira, M.I.; Azeda, C.; Pinto-Correia, T. Management of Montados and Dehesas for High Nature Value: An interdisciplinary pathway. Agrofor. Syst. 2016, 90, 69–85. [Google Scholar] [CrossRef] [Green Version]
  3. Nair, P.K.R.; Gordon, A.M.; Mosquera-Losada, M.R. Agroforestry. In Ecological Engineering: Encyclopedia of Ecology; Academic Press: Oxford, UK, 2008; pp. 101–110. [Google Scholar]
  4. Nerlich, K.; Graeff-Hönninger, S.; Claupein, W. Agroforestry in Europe: A review of the disappearance of traditional systems and development of modern agroforestry practices, with emphasis on experiences in Germany. Agrofor. Syst. 2013, 87, 475–492. [Google Scholar] [CrossRef]
  5. Smith, J.; Pearce, B.D.; Wolfe, M.S. A European perspective for developing modern multifunctional agroforestry systems for sustainable intensification. Renew. Agric. Food Syst. 2012, 27, 323–332. [Google Scholar] [CrossRef]
  6. Sharrow, S.H.; Brauer, D.; Clason, T.R. Silvopastoral Practices. N. Am. Agrofor. Integr. Sci. Pract. 2009, 105–131. [Google Scholar] [CrossRef]
  7. Röhrig, N.; Hassler, M.; Roesler, T. Capturing the value of ecosystem services from silvopastoral systems: Perceptions from selected Italian farms. Ecosyst. Serv. 2020, 44, 101152. [Google Scholar] [CrossRef]
  8. Rois-Díaz, M.; Lovric, N.; Lovric, M.; Ferreiro-Domínguez, N.; Mosquera-Losada, M.R.; den Herder, M.; Graves, A.; Palma, J.H.N.; Paulo, J.A.; Pisanelli, A.; et al. Farmers’ reasoning behind the uptake of agroforestry practices: Evidence from multiple case-studies across Europe. Agrofor. Syst. 2018, 92, 811–828. [Google Scholar] [CrossRef] [Green Version]
  9. Munroe, D.K.; van Berkel, D.B.; Verburg, P.H.; Olson, J.L. Alternative trajectories of land abandonment: Causes, consequences and research challenges. Curr. Opin. Environ. Sustain. 2013, 5, 471–476. [Google Scholar] [CrossRef]
  10. Guillerme, S.; Barcet, H.; de Munnik, N.; Maire, E.; Marais-Sicre, C. Evolution of traditional agroforestry landscapes and development of invasive species: Lessons from the Pyrenees (France). Sustain. Sci. 2020, 15, 1285–1299. [Google Scholar] [CrossRef]
  11. Burriel, C.; Herdon, M.; Tamás, J.; Várallyai, L. Knowledge databank and repository service for agroforestry. J. Agric. Inform. 2017, 8, 33–40. [Google Scholar] [CrossRef]
  12. Cramer, V.A.; Hobbs, R.J.; Standish, R.J. What’s new about old fields? Land abandonment and ecosystem assembly. Trends Ecol. Evol. 2008, 23, 104–112. [Google Scholar] [CrossRef] [PubMed]
  13. Smith, R.K.; Vaughan Jennings, N.; Robinson, A.; Harris, S. Conservation of European hares Lepus europaeus in Britain: Is increasing habitat heterogeneity in farmland the answer? J. Appl. Ecol. 2004, 41, 1092–1102. [Google Scholar] [CrossRef]
  14. Vaughan, N.; Lucas, E.; Harris, S.; White, P.C.L. Habitat associations of European hares Lepus europaeus in England and Wales: Implications for farmland management. J. Appl. Ecol. 2003, 40, 163–175. [Google Scholar] [CrossRef]
  15. Bonino, N.; Montenegro, A. Reproduction of the European hare in Patagonia, Argentina. Acta Theriol. 1997, 42, 47–54. [Google Scholar] [CrossRef] [Green Version]
  16. Edwards, P.J.; Fletcher, M.R.; Berny, P. Review of the factors affecting the decline of the European brown hare, Lepus europaeus (Pallas, 1778) and the use of wildlife incident data to evaluate the significance of paraquat. Agric. Ecosyst. Environ. 2000, 79, 95–103. [Google Scholar] [CrossRef]
  17. Fickel, J.; Schmidt, A.; Putze, M.; Spittler, H.; Ludwig, A.; Streich, W.J.; Pitra, C. Genetic structure of populations of European brown hare: Implications for management. J. Wildl. Manag. 2005, 69, 760–770. [Google Scholar] [CrossRef]
  18. Smith, R.K.; Vaughan Jennings, N.; Harris, S. A quantitative analysis of the abundance and demography of European hares Lepus europaeus in relation to habitat type, intensity of agriculture and climate. Mamm. Rev. 2005, 35, 1–24. [Google Scholar] [CrossRef]
  19. Lavazza, A.; Cooke, B.D. Diseases of lagomorphs. In Lagomorphs: Pikas, Rabbits, and Hares of the World; Smith, A.T., Johnston, C.H., Alves, P., Hackländer, K., Eds.; JHU Press: Baltimore, MD, USA, 2018; ISBN 1421423413. [Google Scholar]
  20. Santilli, F.; Galardi, L. Effect of habitat structure and type of farming on European hare (Lepus europaeus) abundance. Hystrix Ital. J. Mammal. 2016, 27, 120–122. [Google Scholar] [CrossRef]
  21. Santilli, F.; Bagliacca, M.; Paci, G. Density and habitat use of sympatric Brown hares and European rabbits in a Mediterranean farmland area of Tuscany (Central Italy). Ethol. Ecol. Evol. 2015, 27, 233–243. [Google Scholar] [CrossRef]
  22. Sliwinski, K.; Ronnenberg, K.; Jung, K.; Strauß, E.; Siebert, U. Habitat requirements of the European brown hare (Lepus europaeus Pallas 1778) in an intensively used agriculture region (Lower Saxony, Germany). BMC Ecol. 2019, 19, 31. [Google Scholar] [CrossRef] [Green Version]
  23. Karmiris, I.; Platis, P.D.; Kazantzidis, S.; Papachristou, T.G. Diet selection by domestic and wild herbivore species in a coastal Mediterranean wetland. Ann. Zool. Fennici 2011, 48, 233–242. [Google Scholar] [CrossRef]
  24. Castellaro, G.; Orellana, C.L.; Escanilla, J.P. Summer Diet of Horses (Equus ferus caballus Linn.), Guanacos (Lama guanicoe Müller), and European Brown Hares (Lepus europaeus Pallas) in the High Andean Range of the Coquimbo Region, Chile. Animals 2021, 11, 1313. [Google Scholar] [CrossRef] [PubMed]
  25. Morris, C.D.; Derry, J.F.; Hardy, M.B. Effect of cattle and sheep grazing on the structure of Highland Sourveld swards in South Africa. Trop. Grassl. 1999, 33, 111–121. [Google Scholar]
  26. Marion, B.; Bonis, A.; Bouzillé, J.-B. How much does grazing-induced heterogeneity impact plant diversity in wet grasslands? Écoscience 2010, 17, 229–239. [Google Scholar] [CrossRef]
  27. Karmiris, I.E.; Nastis, A.S. Intensity of livestock grazing in relation to habitat use by brown hares (Lepus europaeus). J. Zool. 2007, 271, 193–197. [Google Scholar] [CrossRef]
  28. Karmiris, I.; Nastis, A. Small ruminants as manipulators of brown hare (Lepus europaeus) habitat in kermes oak rangelands. Options Méditerranéennes 2009, 85, 193–197. [Google Scholar]
  29. Bakker, E.S.; Olff, H.; Gleichman, J.M. Contrasting effects of large herbivore grazing on smaller herbivores. Basic Appl. Ecol. 2009, 10, 141–150. [Google Scholar] [CrossRef] [Green Version]
  30. Van der Graaf, A.J.; Bos, D.; Loonen, M.; Engelmoer, M.; Drent, R.H. Short-term and long-term facilitation of goose grazing by livestock in the Dutch Wadden Sea area. J. Coast. Conserv. 2002, 8, 179–188. [Google Scholar] [CrossRef]
  31. Vickery, J.; Gill, J. Managing grassland for wild geese in Britain: A review. Biol. Conserv. 1999, 89, 93–106. [Google Scholar] [CrossRef]
  32. Holechek, J.L.; Pieper, R.D.; Herbel, C.H. Range Management: Principles and Practices; Prentice Hall Publishing: Saddle River, NJ, USA, 2011. [Google Scholar]
  33. Torralba, M.; Fagerholm, N.; Burgess, P.J.; Moreno, G.; Plieninger, T. Do European agroforestry systems enhance biodiversity and ecosystem services? A meta-analysis. Agric. Ecosyst. Environ. 2016, 230, 150–161. [Google Scholar] [CrossRef] [Green Version]
  34. Karmiris, I.; Pappas, I.; Kitsos, M.; Koukoura, Z. Plant cover influences on the use of microhabitats by the European hare (Lepus europaeus) in recently burned rangelands. In Range Science and Life Quality, Proceedings of the 7th Panhellenic Rangeland Congress, Xanthi, Greece, 14–16 October 2010; Hellenic Range and Pasture Society (HERPAS): Thessaloniki, Greece, 2010; pp. 217–222. [Google Scholar]
  35. Litvaitis, J.A.; Titus, K.; Anderson, E.M. Measuring vertebrate use of terrestrial habitats and foods. In Research and Management Techniques for Wildlife and Habitats; The Wildlife Society: Bethesda, MD, USA, 1996; pp. 254–274. [Google Scholar]
  36. Rühl, J.; Pasta, S. Plant succession on Sicilian terraces. Ann. Bot. 2007, 7, 111–126. [Google Scholar]
  37. Rühl, J.; Caruso, T.; Giucastro, M.; La Mantia, T. Olive agroforestry systems in Sicily: Cultivated typologies and secondary succession processes after abandonment. Plant Biosyst. Int. J. Deal. All Asp. Plant Biol. 2011, 145, 120–130. [Google Scholar] [CrossRef]
  38. Davidson, D.W. The Effects of Herbivory and Granivory on Terrestrial Plant Succession. Oikos 1993, 68, 23–35. [Google Scholar] [CrossRef]
  39. van der Meijden, E.; Wijn, M.; Verkaar, H.J. Defence and Regrowth, Alternative Plant Strategies in the Struggle against Herbivores. Oikos 1988, 51, 355. [Google Scholar] [CrossRef]
  40. Papachristou, T.G.; Platis, P.D.; Nastis, A.S. Foraging behaviour of cattle and goats in oak forest stands of varying coppicing age in Northern Greece. Small Rumin. Res. 2005, 59, 181–189. [Google Scholar] [CrossRef]
  41. Papachristou, T.G.; Platis, P.D. The impact of cattle and goats grazing on vegetation in oak stands of varying coppicing age. Acta Oecol. 2011, 37, 16–22. [Google Scholar] [CrossRef]
  42. Papachristou, T.G.; Platis, P.D.; Papachristou, I.; Samara, T.; Spanos, I.; Chavales, E.; Bataka, A. How the structure and form of vegetation in a black locust (Robinia pseudoacacia L.) silvopastoral system influences tree growth, forage mass and its nutrient content. Agrofor. Syst. 2020, 94, 2317–2330. [Google Scholar] [CrossRef]
  43. Weterings, M.J.A.; Zaccaroni, M.; van der Koore, N.; Zijlstra, L.M.; Kuipers, H.J.; van Langevelde, F.; van Wieren, S.E. Strong reactive movement response of the medium-sized European hare to elevated predation risk in short vegetation. Anim. Behav. 2016, 115, 107–114. [Google Scholar] [CrossRef]
  44. Matthiopoulos, J.; Fieberg, J.; Aarts, G.; Beyer, H.L.; Morales, J.M.; Haydon, D.T. Establishing the link between habitat selection and animal population dynamics. Ecol. Monogr. 2015, 85, 413–436. [Google Scholar] [CrossRef]
  45. Panek, M.; Kamieniarz, R. Studies on the European hare. 54. Relationship between density of brown hare Lepus europaeus and landscape structure in Poland in the years 1981–1995. Acta Theriol. 1999, 44, 67–75. [Google Scholar] [CrossRef] [Green Version]
  46. Karmiris, I.; Tsiouvaras, K. Effects of several plant species on the spatial distribution of the European hare (Lepus europaeus) at the microhabitat scale. In Dry Grasslands of Europe: Grazing and Ecosystem Services, Proceedings of 9th European Dry Grassland Meeting (EDGM), Prespa, Greece, 19–23 May 2012; Hellenic Range and Pasture Society (HERPAS): Thessaloniki, Greece, 2012; pp. 169–174. [Google Scholar]
  47. Kuijper, D.P.J.; Bakker, J.P. Unpreferred plants affect patch choice and spatial distribution of European brown hares. Acta Oecol. 2008, 34, 339–344. [Google Scholar] [CrossRef]
  48. Viviano, A.; Mori, E.; Fattorini, N.; Mazza, G.; Lazzeri, L.; Panichi, A.; Strianese, L.; Mohamed, W.F. Spatiotemporal overlap between the European brown hare and its potential predators and competitors. Animals 2021, 11, 562. [Google Scholar] [CrossRef] [PubMed]
Figure 1. Study area (blue line). Available from Google earth (14 August 2019).
Figure 1. Study area (blue line). Available from Google earth (14 August 2019).
Agriculture 12 00678 g001
Figure 2. Mean change in tree (a), shrub (b), and herbage (c) coverage in olive groves, shrubland, and grassland transects from 2002 to 2021.
Figure 2. Mean change in tree (a), shrub (b), and herbage (c) coverage in olive groves, shrubland, and grassland transects from 2002 to 2021.
Agriculture 12 00678 g002
Figure 3. Mean number of hare pellets deposited in olive groves, shrubland and grassland in 2002, 2011, and 2021. Different letters between columns within the same habitat indicate significant differences (p < 0.05).
Figure 3. Mean number of hare pellets deposited in olive groves, shrubland and grassland in 2002, 2011, and 2021. Different letters between columns within the same habitat indicate significant differences (p < 0.05).
Agriculture 12 00678 g003
Table 1. Two-way factorial analysis output with year (three levels: 2002, 2011, 2021) and habitats (three levels: olive groves, shrubland, grassland) as fixed factors and number of hare pellets as the dependent variable.
Table 1. Two-way factorial analysis output with year (three levels: 2002, 2011, 2021) and habitats (three levels: olive groves, shrubland, grassland) as fixed factors and number of hare pellets as the dependent variable.
SourceSum of SquaresdfMean SquareFSig.
Corrected Model360.92845.128.777<0.001
Intercept1124.4511124.45218.749<0.001
Year0.9220.460.0890.915
Habitats304.832152.4229.651<0.001
Year * Habitats55.17413.792.6830.032
Error1341.632615.14
*: interaction between year and habitats, df: degrees of freedom, F: Fisher statistic, Sig.: significance.
Publisher’s Note: MDPI stays neutral with regard to jurisdictional claims in published maps and institutional affiliations.

Share and Cite

MDPI and ACS Style

Karmiris, I.; Papachristou, T.G.; Fotakis, D. Abandonment of Silvopastoral Practices Affects the Use of Habitats by the European Hare (Lepus europaeus). Agriculture 2022, 12, 678. https://doi.org/10.3390/agriculture12050678

AMA Style

Karmiris I, Papachristou TG, Fotakis D. Abandonment of Silvopastoral Practices Affects the Use of Habitats by the European Hare (Lepus europaeus). Agriculture. 2022; 12(5):678. https://doi.org/10.3390/agriculture12050678

Chicago/Turabian Style

Karmiris, Ilias, Thomas G. Papachristou, and Dimitrios Fotakis. 2022. "Abandonment of Silvopastoral Practices Affects the Use of Habitats by the European Hare (Lepus europaeus)" Agriculture 12, no. 5: 678. https://doi.org/10.3390/agriculture12050678

Note that from the first issue of 2016, this journal uses article numbers instead of page numbers. See further details here.

Article Metrics

Back to TopTop