Effects of Domestic and Wild Ungulate Management on Young Oak Size and...

[Full title: Effects of Domestic and Wild Ungulate Management on Young Oak Size and Architecture]

sustainability Article Effects of Domestic and Wild Ungulate Management on Young Oak Size and Architecture Aida L ó pez-S á nchez 1, * , Sonia Roig 1 , Rodolfo Dirzo 2 and Ram ó n Perea 1,2 Citation: López-Sánchez, A.; Roig, S.; Dirzo, R.; Perea, R. Effects of Domestic and Wild Ungulate Management on Young Oak Size and Architecture Sustainability 2021 , 13 , 7930. https://doi.org/10.3390/ su 13147930 Academic Editor: Victor Rolo Received: 25 June 2021 Accepted: 13 July 2021 Published: 15 July 2021 Publisher’s Note: MDPI stays neutral with regard to jurisdictional claims in published maps and institutional affiliations Copyright: © 2021 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 (https:// creativecommons.org/licenses/by/ 4.0/) 1 Departamento de Sistemas y Recursos Naturales, Universidad Polit é cnica de Madrid, 28040 Madrid, Spain; sonia.roig@upm.es (S.R.); ramon.perea@upm.es (R.P.) 2 Department of Biology, Stanford University, Stanford, CA 94305, USA; rdirzo@stanford.edu * Correspondence: aida.lopez@upm.es Abstract: Scattered oaks in traditional silvopastoral systems (i.e., “dehesas”) provide important ecological services. However, livestock intensification applied to these systems over the last century has affected the architecture of young oak plants. This unsuitable rangeland management practice jeopardizes the long-term system sustainability. Here we examine the alterations in architecture of regenerating oak plants in Mediterranean dehesas under three representative management regimes: (1) traditional management with extensive sheep grazing; (2) commercially driven management with extensive cattle grazing, and (3) native deer grazing at moderate stocking rates (<0.11 livestock units × ha − 1 ). Plant architecture was considerably altered in cattle-grazed “dehesas”, finding a 50% reduction in plant height–diameter ratios, compared to sheep-grazed dehesas where plants with higher height–diameter ratios predominated. Young oak plants, however, showed less altered architecture and less probability of damage on shoot apex (0.20-fold difference) in areas with deer grazing at moderate stocking rates. In addition, those young oak plants with multistemmed individual architecture were more stunted (lower values of crown height–diameter ratio) in areas with livestock grazing than wildlife areas (0.78-fold difference). Shrub presence, under all management schemes, helped to increase in plant height, except when shrubs were located under tree canopies. Conversely, plants without shrub protection showed stunted architecture with well-developed basal diameters but short stature. Appropriate sustainable practices should include cattle stocking rate reduction, traditional sheep grazing promotion, nurse shrub preservation and fencing stunted individuals along with pruning basal sprouts. Our study indicates that management may have important consequences on dehesa regeneration via alterations of plant architecture and therefore on system sustainability Keywords: height-diameter ratio; plant architecture; Quercus ilex ; livestock grazing 1. Introduction Human-managed ecosystems featuring scattered trees occur throughout the world, providing important ecological services (e.g., seed source, nutrient enrichment, landscape connectivity functions, shelter; [ 1 ]). Many of these ecosystems are originally derived from dense forests that have been transformed into open agroforestry systems by clearing several trees and then used for grazing [ 1 , 2 ], supporting relatively high biodiversity [ 3 , 4 ]. This results in landscapes with scattered trees or shrubs (woody pastures) used for grazing. Despite their importance, these woody pastures have experienced important anthropogenic impacts such as overgrazing and land use conversion, all of which threaten their long-term persistence, particularly since the 1950 s [ 5 – 7 ]. The lack of tree recruitment is one of the major consequences of such anthropogenic impacts [ 8 ] due to the implementation of inappropriate management practices that negatively affect natural oak ( Quercus spp.) recruitment [ 9 – 11 ]. In particular, some livestock management practices such as the increment of livestock stocking rates (especially in extensive cattle grazing) or sheep replacement by cattle have been often related to oak recruitment failure [ 12 – 15 ]. Sustainability 2021 , 13 , 7930. https://doi.org/10.3390/su 13147930 https://www.mdpi.com/journal/sustainability

Sustainability 2021 , 13 , 7930 2 of 14 Livestock has been regarded as an important part of ecosystem engineering that restructures ecological communities [ 16 , 17 ]. Generally, low levels of herbivory make woody growth and reproduction possible whereas high levels of it impede survival or affect plant development [ 18 ]. The permanent, stressing effect of high herbivory pressure, may not only affect recruitment rates but also patterns of plant recruitment (e.g., via sexual vs. asexual), as well as the architecture and growth patterns of young plants [ 19 ]. Herbivores generally destroy parts of the plants by pulling and trampling, and reduce biomass and cover of the stratum located within their grazing height [ 20 ]. The effects of large herbivores on young plant performance and architecture may in turn determine their probability of progressing from the juvenile stage to the adult (reproductive) stage, delaying or even impeding successful woodland regeneration of the woodland as a whole [ 21 ]. In addition, grazing height differs according to grazer body size. For instance, cattle can browse above 1.5 m high [ 22 ] while sheep typically browse below 1 m high [ 22 ], and red deer ( Cervus elaphus L.) concentrates browsing at around 1 m [ 23 ]. Hence, larger herbivores are potentially able to consume greater proportions of the plant and have greater impacts damage on critical plant growth parts (e.g. apical meristems) In Spain, ecosystems featuring scattered oak trees throughout the landscape, also known as dehesas, are internationally recognized for their ecological, socioeconomic and cultural importance, as well as for supporting high levels of biodiversity [ 2 , 24 ]. Yet, over the last few decades, dehesas have also suffered a dramatic increase of livestock stocking rates, which is often related to oak recruitment failure [ 9 , 13 – 15 , 25 ]. Research so far has primarily focused on the effect of different management schemes on oak recruitment density, both in dehesas [ 9 , 15 ] and other woody pasture lands [ 26 – 28 ]. However, little is known about the effect of different livestock management schemes (e.g., traditional vs. commercially competitive) or the use of wild vs. domestic ungulates on plant architecture and growth patterns of young oaks. Such knowledge is needed to integrate grazing into management schemes and to determine the ecological impact of herbivores on valuable human-dominated ecosystems. In similar oak wood-pastures worldwide, strong reductions in the stature of young plants (seedlings and saplings) have been observed in cattle-grazed areas compared to those without cattle for more than two decades [ 21 , 28 ]. The result is that oak recruits, repeatedly browsed by cattle, become bushy (multi-stemmed individuals), stunted individuals, forming coppice-like trees with multiple stems [ 21 ]. Conversely, it is known that the presence of shrubs in Mediterranean or arid ecosystems may reduce herbivory lethality [ 29 ] by reducing the probability of shoot apex damage [ 30 ], but this in turn may alter the plant architecture that facilitates the transition to plant reproductive stages. Thus, microsite location of young trees in relation to the presence of herbivore foraging patterns may play an important role not only on oak recruitment density [ 15 , 29 ] but also on plant architecture. Despite these relationships, oak architecture (e.g., height– diameter ratio, crown diameter, plant shape) has not been fully investigated across different microsites and under distinct management schemes This study brings together the effects of these two factors, impact of browsing on plant architecture, and the role of potentially protective microsites on young oak plant architecture under three representative management schemes of the Mediterranean scattered oak woodlands (dehesas). These schemes involve cattle, sheep and wildlife rearing (mostly red deer) foraging, under similar ecological conditions and for more than 30 years under the same management scheme. Specifically, we examined the architecture of Quercus ilex L. as this species is the dominant and most representative tree species of dehesas [ 31 ]. We predicted that (1) architectural measures (height, basal diameter and height–diameter ratio) of young plants (seedlings, saplings and oak multi-stemmed individuals) would be significantly modified under the current (>0.11 livestock units per ha, LU ha − 1 ) extensive livestock farming (especially under cattle grazing) than wildlife management with moderate stocking rates (<0.11 LU ha − 1 ); We posit, in particular, that crown height–diameter ratio of oak multi-stemmed individuals will be related to the management scheme, with gleaner oak multi-stemmed individuals under traditional sheep management; (2) the probability of

Sustainability 2021 , 13 , 7930 3 of 14 finding undamaged shoot apexes would be also greater in traditional sheep management (small-sized animals) compared to other representative management schemes involving larger herbivore (wildlife or cattle) management; and (3) microsite location of young plants will affect oak architecture differently depending on the management scheme, with less impact on plant development under shrub protection 2. Materials and Methods 2.1. Study Area The study area (108 km 2 , largely flat and open) involved different oak dehesa systems within Toledo province, Central Spain (39–40 ◦ N, 5 ◦ W). Elevation ranges from 300 to 400 m a.s.l. The climate is Mediterranean oceanic pluvioseasonal [ 32 ], with a mean annual temperature of 15.1 ◦ C and an average annual rainfall of 571 mm. Soils are sandy and acidic with low organic matter content within topsoil (see L ó pez-S á nchez et al. [ 15 ] for details) The study area supports diverse vegetation dominated by open holm oak ( Quercus ilex L subsp. ballota (Desf.) Samp.) woodland with a shrub cover mostly comprised of xerophytic and evergreen species. Shrub cover is low (0.2%, 0.6% and 38.0% in cattle, sheep and wildlife-grazed areas, respectively; [ 33 ]). The herbaceous layer is dominated by subnitrophilous Mediterranean annual communities and therophytic oligotrophic communities (see L ó pez-S á nchez et al. [ 15 ] for details) 2.2. Study Sites Three sites (independent estates) with distinct and representative management (grazing regime) for at least thirty years (i.e., they were not subjected to ploughing, shrubclearing or fire) were selected within the study area. The first one (142 ha), hereafter “Cattle”, consists of commercially driven management (0.33 LU ha − 1 ) of cattle (breed “Avileña negra ib é rica”). The second site (140 ha), hereafter “Sheep”, has been supporting traditional management (0.25 LU ha − 1 ,) of extensive sheep (breed “Talaverana”). Both sites have maintained livestock rearing year-round for the last 40 years and represent the typical managements (stocking rates) for these systems [ 25 , 34 ]. In addition, both sites are fenced off to control livestock movements and prevent wildlife and human access (see L ó pez-S á nchez et al. [ 15 ] for details). Finally, the third site (150 ha) has not supported livestock since 1985 and its management has been devoted to recreational big game hunting, mostly red deer but also some wild boar ( Sus scrofa L.), for the past 50 years, and represents the typical deer management (densities) of Mediterranean hunting properties in oak-dominated woodlands and dehesas [ 35 , 36 ] (see L ó pez-S á nchez et al. [ 15 ]). 2.3. Sample Design and Data Collection We selected nine independent, replicated zones (three zones per site) of 5 ha, each one with similar density of holm oak trees (42.15 ± 11.44 trees ha − 1 ), with similar diameter at breast height (40.40 ± 16.23 cm, see L ó pez-S á nchez et al. [ 15 ] for details). In each zone, eighteen 4 m × 35 m belt transects (separated by 40 m) were established (total n = 162) within which we defined four different microsites: (i) under the tree canopy (hereafter tree), (ii) under the shrub canopy (hereafter shrub), (iii) under the tree and shrub canopy (hereafter tree-shrub) and (iv) in open grasslands (hereafter open). We recorded the microsite and some architectural measures of all oak young plants (height <130 cm) that were found within the transect. The architectural measures were the basal diameter (hereafter, diameter, cm) and the height (cm) of all young plants, measured on the largest diameter shoot in the event of oak multi-stemmed individuals (plants with multiple shoots). We noted whether the apical sprout was browsed, or whether there was no sign of browsing. In the event of oak multi-stemmed individuals, we also measured crossed diameters (the largest one and their perpendicular). The mean of both crossed diameters was used as a single variable (hereafter, crown diameter). Vertebrate herbivory damage was categorized according to its intensity and was assessed for all young plants. Damage categories followed a 0–4 rank of herbivory level [ 28 ]: 0 for plants with no apparent

Sustainability 2021 , 13 , 7930 4 of 14 browsing evidence (hereafter, null damage), 1 for plants with low browsing (1–10% of browsable biomass damaged; hereafter low damage), 2 for plants with moderate browsing (11–40% of browsable biomass damaged; hereafter moderate damage), 3 for plants with high browsing (41–70% of browsable biomass damaged; hereafter high damage), and 4 for plants with maximum browsing (>70% of browsable biomass damaged; hereafter maximum damage, see details in L ó pez-S á nchez et al. [ 28 ] for details) which was considered as unsustainable browsing since plants at this damage level become incapable of developing onto further ontogenetic stages [ 28 , 36 ]. Surveys were conducted at the beginning of spring (March–April 2014), coinciding with the highest browsing damage in most Mediterranean environments [ 37 ]. 2.4. Statistical Analysis We developed generalized linear mixed models (GLMMs, [ 38 ]) for all architectural response variables (Table 1 ). These models are an extension of General Linear Models (e.g., regression, variance analysis) allowing different error distributions for response variables, and establishing a linear relationship through a link function. In addition, applying random effects allows grouped data to be analyzed. We established the shape of the young plants (thickest shoot in the case of multi-stemmed individual oaks) through the height–diameter ratio (hereafter, HDR) by dividing the height/basal diameter (in the same units, cm). In addition, the shape of young oak multi-stemmed individuals was measured through crown height–diameter ratio (hereafter, CHDR, in cm) by dividing the height/crown diameter (in the same units, cm). When necessary, Box–Cox transformations [ 39 ] were applied to data in order to calculate the lambda transformation (power lambda link) [ 40 ] that maximizes the likelihood. Thus, the response variables were fitted to gamma error distribution with their corresponding power lambda link function (Table 1 ). Table 1. Summary of architectural (response) variables Response Variable Sample Size Used (n) Error Distribution (Power Lambda Link Function) 1 Height 554 (all plants) Gamma (0.70) Diameter 174 (plants with basal diameter >1 cm) Gamma (0.70) Height–diameter ratio 554 (all plants) Gamma (0.34) Crown height–diameter ratio 253 (only oak multi-stemmed individuals) Gamma (0.33) 1 Power lambda link function (g( µ ) = µλ ) is the lambda ( λ , numeric value inside the brackets) used for the monotonic transformations All models included rangeland management, microsite and the herbivory occurrence (presence-absence) as fixed effects. The structure of the random effect was the following: transect nested within zone and, thus, nested within management regime. Moreover, we repeated the same analyses for each response variable with the same random effect and fixed effects but including herbivory intensity (using the herbivory categories described above) instead of herbivory occurrence In addition, the occurrence of browsed apical sprout (presence-absence, for plants with some herbivory) was analyzed as a response variable by means of GLMMs and fitted to binomial error distribution with a logit link function. The models included rangeland management and microsite as fixed effects. Transect nested within zone and within management regime was considered as random effect We used the model averaging approach [ 41 ] in all cases. We first fitted the maximal model, containing all the predictors. Then, we performed model comparison of all possible models by using the AIC weights. For model comparison we used the “dredge” function within the “MuMIn” package of R. Finally, we obtained the model-averaged coefficients as well as the relative importance of each predictor (from 0 to 1) by using the “model.avg” function of “MuMIn”. For predicted values obtained from models, we used the “fitted” function within the “stats” basic package of R.

Sustainability 2021 , 13 , 7930 5 of 14 Data processing and statistics were performed using R 3.1.1 [ 42 ] with the modules “lme 4” [ 43 ], “car” [ 44 ] and “MuMIn” [ 45 ]. 3. Results 3.1. Management Effects on Young Oak Plant Architecture Rangeland management affected the height, diameter (>1 cm) and shape (HDR) of the young oaks and multi-stemmed individuals (Table 2 ). In sheep-grazed areas, we found significantly greater heights of young plants (mean of 45 cm) than in cattle-grazed areas (31 cm) and wildlife areas (24 cm; Figure 1 a). In contrast, the diameter of young plants was greater (3.8 cm; Figure 1 a) in cattle-grazed areas than in wildlife areas with no extensive farming (2.6 cm; Figure 1 a). In addition, in areas where only wildlife was present the diameter of young plants was greater than in sheep-grazed areas (2 cm; Figure 1 a). Table 2. Summary of the generalized linear mixed models to analyze the effect of management, occurrence of herbivory and microsite on plant architectural variables (height, diameter and height–diameter ratio, and crown height–diameter ratio) Response Variable Management H.O. 1 Microsite Sheep Wildlife Presence Shrub Tree-Shrub Open Height (cm) Estimated model coefficient 5.088 1.423 6.428 2.626 0.053 − 0.539 Standard error 1.021 0.935 0.517 1.003 0.490 0.548 z-value 4.983 1.522 12.423 2.619 0.109 0.985 p -value <0.001 0.128 <0.001 0.009 0.913 0.325 Diameter (cm) Estimated model coefficient − 0.528 − 0.289 0.271 − 0.662 − 0.719 0.038 Standard error 0.132 0.139 0.127 0.216 0.259 0.103 z-value 4.000 2.076 2.124 3.065 2.779 0.363 p -value <0.001 0.038 0.034 0.002 0.005 0.716 Height–diameter ratio Estimated model coefficient 0.917 0.417 0.445 0.529 0.052 − 0.053 Standard error 0.095 0.091 0.053 0.114 0.073 0.068 z-value 9.604 4.571 8.349 4.634 0.706 0.777 p -value <0.001 <0.001 <0.001 <0.001 0.480 0.437 Crown Height–diameter ratio Estimated model coefficient 0.026 0.104 0.044 0.069 − 0.030 0.002 Standard error 0.039 0.040 0.031 0.053 0.051 0.029 z-value 0.659 2.585 1.390 1.299 0.596 0.072 p -value 0.509 0.010 0.165 0.194 0.551 0.943 1 H.O: Herbivory Occurrence. Reference levels from fixed effects Management, H.O. and Microsite are Cattle, Absence and Tree, respectively As HDR is directly proportional to height measure, we also found higher values of HDR of young plants in sheep-grazed areas (30; Figure 1 a) than in areas where livestock grazing was not present (20; Figure 1 a). Furthermore, in areas where only wildlife was present the HDR of young plants was higher than in cattle-grazed areas (14; Figure 1 a). We found a higher proportion of young oak multi-stemmed individuals in livestock (cattle or sheep)-grazed areas (71.0% ± 40.1 and 68.3% ± 30.7, respectively) than in wildlife areas (58.3% ± 43.6). Multi-stemmed individuals were more stunted (lower CHDR) in livestock grazing areas than in wildlife areas (Table 2 ), but they did not differ between cattleand sheep-grazed areas (Table 2 ). Plants with greater height (50 cm) showed higher probability of being browsed (Table 2 ) exhibiting moderate, high and maximum damages (Figure 2 ). In addition, plants with greater diameter (3.5 cm) showed higher probability of being browsed (Table 2 ) exhibiting high and maximum damage (Figure 2 ).

Sustainability 2021 , 13 , 7930 6 of 14 Sustainability 2021 , 13 , 7930 6 of 14 Figure 1. Architectural variables (height, diameter and height–diameter ratio) of plants depending on ( a ) the management regime (shown through the bars); and ( b ) the microsite (shown through the bars). N = 554 plants for height and height– diameter ratio, and N = 176 plants for diameter as response variables. Error lines are 95% confidence intervals. Different letters (a, b, c) indicate significant differences (p < 0.05 ) in architectural variables between ( a ) management regime and ( b ) microsite. As HDR is directly proportional to height measure, we also found higher values of HDR of young plants in sheep-grazed areas (30; Figure 1 a) than in areas where livestock grazing was not present (20; Figure 1 a). Furthermore, in areas where only wildlife was present the HDR of young plants was higher than in cattle-grazed areas (14; Figure 1 a). We found a higher proportion of young oak multi-stemmed individuals in livestock (cattle or sheep)-grazed areas (71.0% ± 40.1 and 68.3% ± 30.7, respectively) than in wildlife areas (58.3% ± 43.6). Multi-stemmed individuals were more stunted (lower CHDR) in livestock grazing areas than in wildlife areas (Table 2), but they did not differ between cattleand sheep-grazed areas (Table 2). Figure 1. Architectural variables (height, diameter and height–diameter ratio) of plants depending on ( a ) the management regime (shown through the bars); and ( b ) the microsite (shown through the bars). N = 554 plants for height and height– diameter ratio, and N = 176 plants for diameter as response variables. Error lines are 95% confidence intervals. Different letters (a, b, c) indicate significant differences ( p < 0.05) in architectural variables between ( a ) management regime and ( b ) microsite.

Sustainability 2021 , 13 , 7930 7 of 14 Figure 2. Probability of browsing depending on plant architectural variables (plant height, diameter and height–diameter ratio, and multi-stemmed individual crown height–diameter ratio). N = 554 plants for height and height–diameter ratio, N = 176 plants for diameter, and N = 253 multi-stemmed individuals as response variables. Bars indicate plant architectural variable value between different levels of damage intensity. Null damage: browsable biomass undamaged; Low damage: 1–10% of browsable biomass damaged; Moderate damage: 11–40% of browsable biomass damaged; High damage: 41–70% of browsable biomass damaged; Maximum damage: >70% of browsable biomass damaged. Error lines are 95% confidence intervals. Different letters (a, b, c) indicate significant differences ( p < 0.05) in architectural variables between different levels of herbivory damage intensity Plants with greater HDR (30) showed higher probability of being browsed (Table 2 ) for any score of herbivory intensity (Figure 2 ). We did not find differences in oak multistemmed individuals CHDR depending on occurrence and intensity of herbivory (Table 1 , Figure 2 ). 3.2. Microsite Effects on Young Holm Oak Architecture Microsite of location affected the height, diameter (>1 cm) and shape (HDR) of the young oaks (Table 2 ). However, we did not find differences in shape of oak multi-stemmed individuals (CHDR) depending on the microsite (Table 2 ). Young oak plants refuged under shrubs located in open areas showed greater values of heights (mean of 37 cm) than in other microsites (around 20 cm; Figure 1 b). In contrast, we found significantly greater diameters in open areas and under tree canopy cover (2.8 cm) than under shrubs located both in open areas and under tree canopy cover (1.5; Figure 1 b). Additionally, we found higher HDR (30) under shrub cover than in other microsites (18; Figure 1 b). 3.3. Damage on Shoot Apex Occurrence of intact shoot apex (no apical sprout damage) in young plants varied depending on the management regime (Table 3 ). In livestock (cattle or sheep)-grazed areas

Sustainability 2021 , 13 , 7930 8 of 14 the probability of having a damaged shoot apex was greater than in wildlife areas. We did not find differences on shoot apex damage across microsites (Table 3 ). Table 3. Summary of the generalized linear mixed models to analyze the effect of management and microsite on the occurrence of apical sprout damage Response Variable Predictors Factors Estimated Model Coefficient Standard Error z -Value p -Value Probability of occurrence of apical sprout damage Intercept 0.706 0.739 0.954 0.340 Management Sheep − 0.060 0.977 0.061 0.951 Wildlife − 3.494 0.983 3.557 <0.001 Shrub 0.699 0.688 1.017 0.309 Tree-shrub − 0.153 0.639 0.239 0.810 Microsite Open 0.695 0.393 1.769 0.077 4. Discussion 4.1. Management Effects on Young Oak Plant Architecture The different management schemes led to a notable change in young oak recruitment architecture. We observed lower (40%) oak heights for areas with a management of commercial extensive cattle grazing in comparison to more traditional management such as sheep farming. Alternative management schemes with no extensive farming (at least 30 years without livestock) also reduced the young oak height in comparison to traditional sheep-grazed areas but the effect was less accentuated (around 30% height reduction) than with highly competitive cattle-grazing areas. Here, we found that plant architecture was modified, increasing the abundance of oak multi-stemmed individuals, with a clear shaping of the natural tree form (Figure 1 ). At stand level, an important consequence of abundant presence of young oak plants (height < 1.30 m) with low height–diameter ratios is the increase of the time required to reach the height threshold (1.5–2 m) that allows young trees to avoid being browsed [ 46 , 47 ]. In addition, stunted individuals with low height have greater probability of being killed by large browsers [ 48 ]. Importantly, we found a higher probability of shoot apex damage under permanent livestock farming (cattle or sheep), compared with representative wildlife areas, probably due to the continuous browsing activity of cattle and sheep (management under continuous grazing). Areas with no extensive farming (wildlife) usually involve lower stocking rates due to both lower animal density and greater mobility of wild ungulates. The continuous disruption of apical dominance through shoot apex removal results in shorter plants with multiple lateral meristems that facilitate the increase in width growth. This differential growth in width vs. height delays plant development and brings about a higher probability of being repeatedly damaged, either by browsing or by trampling [ 49 ]. Accordingly, we found larger basal diameters in cattle areas compared to wildlife areas, or with traditional management of sheep (Figure 1 ). This corroborates the idea of a disproportionally height–diameter ratio According to Plieninger [ 6 ], dehesas with long-term silvopastoral use (>300 years) maintain adult or sub-adult trees with greater diameters than those with less historical silvopastoral management (60–100 years). Most of those adult or sub-adult trees are thick and have great diameter; but their height is not large enough to represent a well-developed adult tree. Our results showed that cattle farming management, involving continuous grazing at high stocking rates, resulted in a strong limitation for the growth of young oak plants and confirms previous studies [ 21 , 28 , 50 ]. Differences in HDR across management schemes need to be considered with caution since it may involve both management (stocking rates, presence) and animal size. Larger herbivores will reach the central shoot more easily than smaller herbivores. Most of the young oak plants in dehesas generated sprouts as a response to herbivore damage, and as soon as the horizontal extension of the stools is thick enough, the central shoot can gain height without being accessible to browsing herbivores [ 51 ]. Sheep are less able to reach the central shoot due to their smaller body size and, thus, young plants with certain height or width (e.g., wider oak multi-stemmed individuals) will escape shoot apex damage more easily, growing with higher HDR, which, in turn, results in the ability to

Sustainability 2021 , 13 , 7930 9 of 14 advance to the adult stage faster. Moreover, slender young plants (higher HDR) showed a higher probability of being browsed since they were more visible and accessible than stunted plants Most oak regeneration found in examined livestock-grazed areas was in the form of oak multi-stemmed individuals (70%) due to high herbivore pressure, as happens in many dehesas holding livestock [ 9 , 25 ]. Our study reveals that livestock management exerted over more than 30 years results in more stunted plants (lower CHDR values) than in the case of wildlife grazing at moderate stocking rates (<0.11 LU ha − 1 ) due to the longer and continued consumption over oak multi-stemmed individuals. In particular, intensive commercial management of cattle sustained stunted oak multi-stemmed individuals (compared to traditional management of sheep grazing), resulting in protection of the central shoot against damage caused by cattle in this type of management. However, these extensive oak multi-stemmed individuals could not avoid constant damage in their central shoot after more than 30 years due to the current, most competitive management, involving constant presence of the cattle (year-round) at high stocking rates (>0.30 LU ha − 1 ) 4.2. Microsite Effects on Young Holm Oak Architecture Young holm oak architecture was related to specific microsites. We found greater plant height under shrub protection in open areas. In harsh, dry environments, such as the Mediterranean, shrub cover not only provides protection against herbivore pressure [ 25 , 30 ], but also reduces evapotranspiration [ 52 , 53 ], which favors the growth of the apical shoot, leading to higher plants [ 52 , 54 ] with greater HDR (Figure 1 ). Thus, the results of our study are in line with previous research showing that the presence of some shrubs in Mediterranean dehesas may have positive effects on early recruitment of oak species, not only by facilitating seedling establishment [ 33 , 50 , 53 , 55 ], but also by ensuring a more natural plant architecture (reduction of apical damage) and a faster advance to the reproductive stage [ 15 ]. Plants under shrub protection located under trees were also protected against intensive browsing and desiccation. However, competition for light conditions and other resources is probably too high given the number of oak shoots under tree cover and the presence of the adult trees, which may reduce plant growth, affecting architecture. Conversely, we found higher diameter and smaller HDR under tree canopy and in open areas (without shrub protection) in comparison to those growing under shrub cover (Figure 1 ). 4.3. Sustainable Management Involves Well-Developed Young Oak Plants The current age structure in dehesas (scarce adult oaks and lack of regeneration) represents a threat to the sustainability of the whole system because old-aged trees are not being replaced [ 9 , 13 ]. L ó pez-S á nchez et al. [ 15 ] have shown the striking differences in oak densities and herbivory role under three representative management schemes of Mediterranean dehesas. In the present study, we analyze the architecture of young oak plants subjected to these three typical management schemes in dehesas. It is not only important to evaluate the numerical oak recruitment presence but also the long-term effects of management (>30 years) on plant architecture and growth. Our results have shown that some livestock management schemes, chiefly high commercially competitive management of cattle, are generating stunted plants due to constant and heavy herbivore pressure over the same plants. However, traditional management of sheep grazing generated slender plants and promoted central shoot development compared to cattle grazing. Therefore, the management recommendation to return to a traditional livestock grazing management (e.g., using local sheep breeds) suggested by L ó pez-S á nchez et al. [ 15 ] would help plants grow faster, and with an adequate architecture that will ensure a more rapid and higher quality regeneration (i.e., incorporation of well-developed reproductive trees in less time). Furthermore, it might be helpful to reduce those Supplementary feed with high urea content that disproportionally make animals search for browse [ 56 ]. Additionally, temporary livestock exclusion with only the presence of wildlife (deer) at adequate densities (<0.11 LU ha − 1 ) will provide opportunities for holm oak regeneration and a possible

Sustainability 2021 , 13 , 7930 10 of 14 encroachment of shrub cover [ 57 ] that would help to protect young plants. However, high densities of deer could produce an opposite result [ 36 , 58 , 59 ], since deer also browse and are large-bodied animals that impede oak regeneration and can modify the architecture of young oaks [ 16 ]. Therefore, under wildlife management it is also essential to monitor and control deer populations [ 60 , 61 ]. Young plants should not only substitute the actual old stand but also ensure the future sustainability of the whole system by producing high acorn yield. Hence, individual protection may be essential in current livestock management schemes, especially in high commercially competitive management, along with shearing epicormic and basal sprouts [ 31 ]. This management practice should promote greater HDR, reducing the disproportional horizontal extension of the sprouts. In addition, this technique will generate larger saplings in a shorter amount of time and will give rise to reproductive trees. We may remove the individual protection after the saplings reach the grazing height threshold (>2 m). Herbivores will then browse lower parts of the plant, operating as a pruning mechanism with no effect on upper parts [ 62 ]. Examples of these techniques are shown in Figure 3 and clearly deserve further investigation. The use of oak multi-stemmed individuals or stunted saplings to generate reproductive trees through protection and pruning could be more promising (both economically and environmentally) than planting new individuals. For instance, protecting oak multi-stemmed individuals and saplings instead of planting imported trees will reduce the risk of introducing important diseases (e.g., sudden oak death caused by Phytophthora spp.) that have been commonly brought through the introduction of plant and soil material from nurseries. Further research is needed to fully evaluate the costs and benefits of these proposed management practices Sustainability 2021 , 13 , 7930 11 of 14 Figure 3. Protection of two stunted multi-stemmed individuals of oak ( Quercus ilex ) with a strong wire fence (2 m high). Only part of the oak multi-stemmed individuals was protected. Pictures show a comparison between the protected part and the original part (non-protected oak multi-stemmed individuals): ( a ) cylindrical shape of the protected part of the multi-stemmed individuals, showing an increase in height (>2 m high) and no pruning was carried out; and ( b ) small tree generated from a multi-stemmed individual after partial protection and pruning of the basal sprouts 5. Conclusions Livestock intensification (especially in high commercially competitive management with cattle grazing) applied to silvopastoral systems over the last century has affected the architecture of young oak plants, potentially reducing the probability of high acorn yield Figure 3. Cont .

Sustainability 2021 , 13 , 7930 11 of 14 Sustainability 2021 , 13 , 7930 11 of 14 Figure 3. Protection of two stunted multi-stemmed individuals of oak ( Quercus ilex ) with a strong wire fence (2 m high). Only part of the oak multi-stemmed individuals was protected. Pictures show a comparison between the protected part and the original part (non-protected oak multi-stemmed individuals): ( a ) cylindrical shape of the protected part of the multi-stemmed individuals, showing an increase in height (>2 m high) and no pruning was carried out; and ( b ) small tree generated from a multi-stemmed individual after partial protection and pruning of the basal sprouts 5. Conclusions Livestock intensification (especially in high commercially competitive management with cattle grazing) applied to silvopastoral systems over the last century has affected the architecture of young oak plants, potentially reducing the probability of high acorn yield Figure 3. Protection of two stunted multi-stemmed individuals of oak ( Quercus ilex ) with a strong wire fence (2 m high). Only part of the oak multi-stemmed individuals was protected. Pictures show a comparison between the protected part and the original part (non-protected oak multi-stemmed individuals): ( a ) cylindrical shape of the protected part of the multi-stemmed individuals, showing an increase in height (>2 m high) and no pruning was carried out; and ( b ) small tree generated from a multi-stemmed individual after partial protection and pruning of the basal sprouts. The following Photos: Ramón Perea 5. Conclusions Livestock intensification (especially in high commercially competitive management with cattle grazing) applied to silvopastoral systems over the last century has affected the architecture of young oak plants, potentially reducing the probability of high acorn yield of future adult trees. This rangeland management practice jeopardizes the long-term system sustainability. Specifically, cattle-grazed “dehesas” feature considerably altered plant architecture by reducing 50% plant height–diameter ratios compared to traditional management with extensive sheep grazing. In contrast, young oak plants showed more natural architecture and less probability of damage on shoot apex in areas with deer grazing at moderate stocking rates. Shrub presence, for all management schemes, helped to increase plant height, except when shrubs were located under tree canopies Hence, we recommend sustainable practices such as cattle stocking rate reduction, traditional sheep grazing promotion, nurse shrub preservation and the fencing of stunted individuals along with pruning basal sprouts. Overall, our study highlights that management may have important consequences for dehesa regeneration via alterations of plant architecture and for the sustainability of the systems Author Contributions: Conceptualization, A.L.-S., R.P. and S.R.; formal analysis, A.L.-S.; data curation, A.L.-S.; writing—original draft preparation, A.L.-S.; writing—review and editing, R.P. and R.D.; supervision, R.P. and S.R. All authors have read and agreed to the published version of the manuscript Funding: This research was funded by a Study Fellowship (‘FPU’) of the Spanish Ministry of Education, Culture and Sport to A.L.-S., a Marie Curie fellowship from the European Union (FP 7- PEOPLE-2013-IOF-627450) to R.P., and the project GLOBALFOR supported by UPM and Comunidad

Sustainability 2021 , 13 , 7930 12 of 14 de Madrid (Convenio Plurianual for young researchers). RD was supported by Stanford’s unrestricted funds to Dirzo Lab Institutional Review Board Statement: “Not applicable.” Field studies did not involve endangered or protected species. Animals were only observed in the field, and were not captured or harmed in any way Data Availability Statement: The data presented in this study are openly available in the FigShare Repository at https://doi.org/10.6084/m 9.figshare.14955483.v 1 (accessed on 11 July 2021). L ó pez- S á nchez: Aida; Sonia Roig; Dirzo, Rodolfo; Perea, Ram ó n (2021): Effects of domestic and wild ungulate management on young oak size and architecture. figshare. Dataset https://doi.org/10.608 4/m 9.figshare.14955483.v 1 (accessed on 11 July 2021) Acknowledgments: We thank the staff of “Dehes ó n del Encinar”, especially Celia L ó pez-Carrasco and Antonio Á vila Cerrada, for their help to access the ranch and help to contact ranch owners. We thank Arturo Cobisa P é rez for access at the “Dehesa nueva” and Luis Fernando G ó mez Calvo for access at the “Valdecasillas”. We thank Irma Vasquez Garc í a for her assistance in the field Conflicts of Interest: The authors declare no conflict of interest References 1 Manning, A.D.; Fischer, J.; Lindenmayer, D.B. Scattered trees are keystone structures–implications for conservation Biol. Conserv 2006 , 132 , 311–321. [ CrossRef ] 2 Moreno, G.; Pulido, F.J. The functioning, management and persistence of dehesas. In Agroforestry in Europe ; Springer: Berlin/Heidelberg, Germany, 2009; pp. 127–160 3 Myers, N.; Mittermeier, R.A.; Mittermeier, C.G.; da Fonseca, G.A.; Kent, J. Biodiversity hotspots for conservation priorities Nature 2000 , 403 , 853–858. [ CrossRef ] [ PubMed ] 4 Eichhorn, M.; Paris, P.; Herzog, F.; Incoll, L.; Liagre, F.; Mantzanas, K.; Mayus, M.; Moreno, G.; Papanastasis, V.; Pilbeam, D. Silvoarable systems in Europe–past, present and future prospects Agrofor. Syst 2006 , 67 , 29–50. [ CrossRef ] 5 Fern á ndez-Al é s, R.; Martin, A.; Ortega, F.; Ales, E.E. Recent changes in landscape structure and function in a Mediterranean region of SW Spain (1950–1984) Landsc. Ecol 1992 , 7 , 3–18. [ CrossRef ] 6 Plieninger, T. Habitat loss, Fragmentation, and Alteration–Quantifying the Impactof Land-use Changes on a Spanish Dehesa Landscape by Use of Aerial Photography and GIS Landsc. Ecol 2006 , 21 , 91–105. [ CrossRef ] 7 Underwood, E.C.; Viers, J.H.; Klausmeyer, K.R.; Cox, R.L.; Shaw, M.R. Threats and biodiversity in the mediterranean biome Divers. Distrib 2009 , 15 , 188–197. [ CrossRef ] 8 Gibbons, P.; Lindenmayer, D.B.; Fischer, J.; Manning, A.D.; Weinberg, A.; Seddon, J.; Ryan, P.; Barrett, G. The future of scattered trees in agricultural landscapes Conserv. Biol 2008 , 22 , 1309–1319. [ CrossRef ] 9 Pulido, F.J.; D í az, M.; de Trucios, S.J.H. Size structure and regeneration of Spanish holm oak Quercus ilex forests and dehesas: Effects of agroforestry use on their long-term sustainability For. Ecol. Manag 2001 , 146 , 1–13. [ CrossRef ] 10 Tyler, C.M.; Kuhn, B.; Davis, F.W. Demography and recruitment limitations of three oak species in California Q. Rev. Biol 2006 , 81 , 127–152. [ CrossRef ] 11 Plieninger, T.; Schaich, H.; Kizos, T. Land-use legacies in the forest structure of silvopastoral oak woodlands in the Eastern Mediterranean Reg. Environ. Chang 2011 , 11 , 603–615. [ CrossRef ] 12 Hostert, P.; Röder, A.; Hill, J.; Udelhoven, T.; Tsiourlis, G. Retrospective studies of grazing-induced land degradation: A case study in central Crete, Greece Int. J. Remote Sens 2003 , 24 , 4019–4034. [ CrossRef ] 13 Plieninger, T.; Pulido, F.J.; Konold, W. Effects of land-use history on size structure of holm oak stands in Spanish dehesas: Implications for conservation and restoration Environ. Conserv 2003 , 30 , 61–70. [ CrossRef ] 14 Cierjacks, A.; Hensen, I. Variation of stand structure and regeneration of Mediterranean holm oak along a grazing intensity gradient Plant Ecol 2004 , 173 , 215–223. [ CrossRef ] 15 L ó pez-S á nchez, A.; Perea, R.; Dirzo, R.; Roig, S. Livestock vs. wild ungulate management in the conservation of Mediterranean dehesas: Implications for oak regeneration For. Ecol. Manag 2016 , 362 , 99–106. [ CrossRef ] 16 Waller, D.M.; Alverson, W.S. The white-tailed deer: A keystone herbivore Wildl. Soc. Bull 1997 , 217–226 17 Derner, J.D.; Lauenroth, W.K.; Stapp, P.; Augustine, D.J. Livestock as ecosystem engineers for grassland bird habitat in the western Great Plains of North America Rangel. Ecol. Manag 2009 , 62 , 111–118. [ CrossRef ] 18 D í az, M.; Pulido, F.J.; Møller, A.P. Herbivore effects on developmental instability and fecundity of holm oaks Oecologia 2004 , 139 , 224–234. [ CrossRef ] 19 Møller, A.P.; Shykoff, J.A. Morphological developmental stability in plants: Patterns and causes Int. J. Plant Sci 1999 , 160 , S 135–S 146. [ CrossRef ] 20 Milchunas, D.G.; Lauenroth, W.K. Quantitative effects of grazing on vegetation and soils over a global range of environments Ecol. Monogr 1993 , 63 , 327–366. [ CrossRef ]

Sustainability 2021 , 13 , 7930 13 of 14 21 Garbarino, M.; Bergmeier, E. 7 Plant and vegetation diversity in European wood-pastures. In European Wood-Pastures in Transition: A Social-Ecological Approach ; Hartel, T., Plieninger, T., Eds.; Routledge: Abingon, UK, 2014; pp. 113–131 22 Sanon, H.; Kabor é -Zoungrana, C.; Ledin, I. Behaviour of goats, sheep and cattle and their selection of browse species on natural pasture in a Sahelian area Small Rumin. Res 2007 , 67 , 64–74. [ CrossRef ] 23 Renaud, P.-C.; Verheyden-Tixier, H.; Dumont, B. Damage to saplings by red deer ( Cervus elaphus ): Effect of foliage height and structure For. Ecol. Manag 2003 , 181 , 31–37. [ CrossRef ] 24 Plieninger, T.; Wilbrand, C. Land use, biodiversity conservation, and rural development in the dehesas of Cuatro lugares , Spain Agrofor. Syst 2001 , 51 , 23–34. [ CrossRef ] 25 Plieninger, T.; Pulido, F.J.; Schaich, H. Effects of land-use and landscape structure on holm oak recruitment and regeneration at farm level in Quercus ilex L. dehesas J. Arid Environ 2004 , 57 , 345–364. [ CrossRef ] 26 McClaran, M.P.; Bartolome, J.W. Effect of Quercus douglasii (Fagaceae) on herbaceous understory along a rainfall gradient Madroño 1989 , 36 , 141–153 27 Dufour-Dror, J.-M. Influence of cattle grazing on the density of oak seedlings and saplings in a Tabor oak forest in Israel Acta Oecol 2007 , 31 , 223–228. [ CrossRef ] 28 L ó pez-S á nchez, A.; Schroeder, J.; Roig, S.; Sobral, M.; Dirzo, R. Effects of cattle management on oak regeneration in northern Californian Mediterranean oak woodlands PLoS ONE 2014 , 9 , e 105472. [ CrossRef ] [ PubMed ] 29 Rolo, V.; Plieninger, T.; Moreno, G. Facilitation of holm oak recruitment through two contrasted shrubs species in Mediterranean grazed woodlands J. Veg. Sci 2013 , 24 , 344–355. [ CrossRef ] 30 Perea, R.; Gil, L. Shrubs facilitating seedling performance in ungulate-dominated systems: Biotic versus abiotic mechanisms of plant facilitation Eur. J. For. Res 2014 , 133 , 525–534. [ CrossRef ] 31 Serrada, R.; San Miguel, A Selvicultura en Dehesas ; Serrada, R., Montero, G., Reque, J.A., Eds.; INIA-Fundaci ó n Conde del Valle de Salazar: Madrid, Spain, 2008; Volume 1178, pp. 861–876 32 Rivas-Mart í nez, S.; Rivas-Saenz, S. Worldwide Bioclimatic Classification System 1996–2017. Available online: http://www. globalbioclimatics.org (accessed on 22 November 2017) 33 Perea, R.; L ó pez-S á nchez, A.; Roig, S. The use of shrub cover to preserve Mediterranean oak dehesas: A comparison between sheep, cattle and wild ungulate management Appl. Veg. Sci 2016 , 19 , 244–253. [ CrossRef ] 34 Escribano, M.; Rodr í guez, A.; Mes í as, F.J.; Pulido, F. Niveles de cargas ganaderas en la dehesa extremeña Arch. Zootec 2002 , 51 , 315–326 35 Acevedo, P.; Ruiz-Fons, F.; Vicente, J.; Reyes-Garc í a, A.; Alzaga, V.; Gort á zar, C. Estimating red deer abundance in a wide range of management situations in Mediterranean habitats J. Zool 2008 , 276 , 37–47. [ CrossRef ] 36 Perea, R.; Girardello, M.; San Miguel, A. Big game or big loss? High deer densities are threatening woody plant diversity and vegetation dynamics Biodivers. Conserv 2014 , 23 , 1303–1318. [ CrossRef ] 37 Perea, R.; Perea-Garc í a-Calvo, R.; D í az-Ambrona, C.G.; San Miguel, A. The reintroduction of a flagship ungulate Capra pyrenaica: Assessing sustainability by surveying woody vegetation Biol. Conserv 2015 , 181 , 9–17. [ CrossRef ] 38 Zuur, A.F.; Ieno, E.N.; Walker, N.J.; Saveliev, A.A.; Smith, G.M. Mixed effects modelling for nested data. In Mixed Effects Models and Extensions in Ecology with R ; Springer: Berlin/Heidelberg, Germany, 2009; pp. 101–142 39 Box, G.E.; Cox, D.R. An analysis of transformations J. R. Stat. Soc. Ser. B Methodol 1964 , 26 , 211–252. [ CrossRef ] 40 Crawley, M.J The R Book ; John Wiley & Sons: Hoboken, NJ, USA, 2012 41 Burnham, K.P.; Anderson, D.R Model Selection and Multi-Model Inference: A Practical Information-Theoretic Approach , 2 nd ed.; Springer: New York, NY, USA, 2002 42 R Development Core Team R: A Language and Environment for Statistical Computing ; Foundation for Statistical Computing: Vienna, Austria, 2015 43 Bates, D.; Maechler, M.; Bolker, B.; Walker, S. Fitting Linear Mixed-Effects Models Using lme 4 J. Stat. Softw 2015 , 67 , 1–48 [ CrossRef ] 44 Fox, J.; Weisberg, S An {R} Companion to Applied Regression ; Sage: Thousand Oaks, CA, USA, 2011 45 Barton, K MuMIn: Multi-Model Inference. R Package Version 1.15.1 , 2015 46 P é rez-F é rnandez, M.A.; Gomez-Guti é rrez, J.M. Evolution of the tree cover (Quercus pyrenaica Willd and Quercus ilex subspecies ballota (Desf. Samp) in a dehesa over the last 100 years Cah. Options M é diterran é ennes 1995 , 12 , 259–266 47 Zamora, R.; G ó mez, J.M.; H ó dar, J.A.; Castro, J.; Garc í a, D. Effect of browsing by ungulates on sapling growth of Scots pine in a Mediterranean environment: Consequences for forest regeneration For. Ecol. Manag 2001 , 144 , 33–42. [ CrossRef ] 48 Bartolome, J.W.; McClaran, M.P.; Allen-Diaz, B.H.; Ford, L.D.; Standiford, R.B.; McDougald, N.K.; Forero, L.C. Effects of fire and browsing on regeneration of blue oak. In Oaks in California’s Changing Landscapes, Proceedings of the 5 th Symposium on Oak Woodlands ; Standiford, R., McCreary, D., Purcell, K., Eds.; General Technical Report PSW-GTR-184; PSRS, Forest Service: Albany, CA, USA; USDA: San Diego, CA, USA, 2001; pp. 281–286 49 Aarssen, L.W. Hypotheses for the evolution of apical dominance in plants: Implications for the interpretation of overcompensation Oikos 1995 , 74 , 149–156. [ CrossRef ] 50 Carmona, C.P.; Azc á rate, F.M.; Oteros-Rozas, E.; Gonz á lez, J.A.; Peco, B. Assessing the effects of seasonal grazing on holm oak regeneration: Implications for the conservation of Mediterranean dehesas Biol. Conserv 2013 , 159 , 240–247. [ CrossRef ]

Sustainability 2021 , 13 , 7930 14 of 14 51 San Miguel, A La Dehesa Española: Origen, Tipolog í a, Caracter í sticas y Gesti ó n ; Fundaci ó n Conde del Valle Salazar: Madrid, Spain, 1994; p. 96 52 Castro, J.; Zamora, R.; H ó dar, J.A.; G ó mez, J.M. Use of shrubs as nurse plants: A new technique for reforestation in Mediterranean mountains Restor. Ecol 2002 , 10 , 297–305. [ CrossRef ] 53 G ó mez-Aparicio, L.; Zamora, R.; G ó mez, J.M.; H ó dar, J.A.; Castro, J.; Baraza, E. Applying plant facilitation to forest restoration: A meta-analysis of the use of shrubs as nurse plants Ecol. Appl 2004 , 14 , 1128–1138. [ CrossRef ] 54 Pulido, F.J.; D í az, M. Regeneration of a Mediterranean oak: A whole-cycle approach Ecoscience 2005 , 12 , 92–102. [ CrossRef ] 55 Pulido, F.; Garc í a, E.; Obrador, J.J.; Moreno, G. Multiple pathways for tree regeneration in anthropogenic savannas: Incorporating biotic and abiotic drivers into management schemes J. Appl. Ecol 2010 , 47 , 1272–1281. [ CrossRef ] 56 San Miguel, A. La vegetaci ó n arb ó rea. In Manual de Buenas Pr á cticas de Gesti ó n en Fincas de Montes Mediterr á neo de la Red Natura 2000 ; Gonz á lez, L.M., San Miguel, A., Eds.; Direcci ó n General para la Biodiversidad; Ministerio de Medio Ambiente: Madrid, Spain, 2005; pp. 157–176 57 Ram í rez, J.A.; D í az, M. The role of temporal shrub encroachment for the maintenance of Spanish holm oak Quercus ilex dehesas For. Ecol. Manag 2008 , 255 , 1976–1983. [ CrossRef ] 58 Mysterud, A. The concept of overgrazing and its role in management of large herbivores Wildl. Biol 2006 , 12 , 129–141. [ CrossRef ] 59 Gill, R.M.A.; Morgan, G. The effects of varying deer density on natural regeneration in woodlands in lowland Britain Forestry 2010 , 83 , 53–63. [ CrossRef ] 60 Olea, L.; San Miguel, A. The Spanish Dehesa. A Traditional Mediterranean Silvopastoral System Linking Production and Nature Conservation. In the 21 st General Meeting of the European Grassland Federation ; European Grassland Federation: Kassel, Germany, 2006; pp. 3–11 61 Mart í nez-Ja ú regui, M.; Arenas, C.; Herruzo, A.C. Understanding long-term hunting statistics: The case of Spain (1972–2007) For. Syst 2011 , 20 , 139–150. [ CrossRef ] 62 Perea, R. Bellotas: El esperado man á Trofeo. Caza Conserv 2012 , 511 , 60–65.