Aleppo pine stands can be made more resilient to disturbances such as forest fires, by introducing native and resprouting hardwood species. Pine density impacts seedling establishment by modifying resource availability and abiotic stress. Under Mediterranean conditions, moderate thinning (15–20 m 2 /ha) was the most effective in promoting the establishment and growth of a number of hardwood species.
Developing silvicultural methods to help Mediterranean forests adapt to climate change is of high importance. Introducing resprouting hardwood species below pine stands is expected to promote diversity and resilience of these stands, particularly to forest fires.
The aim of this study was to examine how the intensity of pine thinning influences understory microenvironment and the establishment of various hardwood seedlings in two Mediterranean sites.
Aleppo pine stands were thinned down to three levels of basal area (uncut 30 m2/ha, moderate thinning 13–20 m2/ha, heavy thinning 7–10 m2/ha) at two Mediterranean sites (South-East France and South-East Spain). Seedlings of six hardwood species were introduced in the understory, and their survival and growth were monitored and related to changes in microenvironment induced by thinning.
At both sites, thinning improved light availability and seedling diameter increment of all target species. Thinning increased extreme temperature and evaporative demand. Heavy thinning increased summer soil moisture in SE Spain but not in SE France. The worst conditions for seedling survival were reached under uncut stands in SE France and low-density stands in SE Spain.
Thinning in pine stands accelerated seedling growth, but excessive thinning worsened summer drought and affected seedling survival. Moderate thinning (15–20 m2/ha) seems to be the best option in support of the introduction of hardwoods in the understory, which can improve forest diversity and resilience in the future.
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Forest fires, drought, extreme events, and pest outbreaks are all predicted to increase in the Mediterranean Basin (Kovats et al. 2014; Moriondo et al. 2006). In this context, it is vital to develop silvicultural methods that increase the resistance and resilience of Mediterranean forests to environmental perturbations (Lindner et al. 2008).
Over the last few decades, Mediterranean forests have experienced a rapid expansion of pioneer conifer stands, driven by natural colonization after land abandonment in SE France (Barbero et al. 1990) or afforestation efforts in SE Spain (Ortuño 1990). This expansion process is particularly visible in Aleppo pine (Pinus halepensis), forming dense monospecific stands that are highly flammable and facilitate the spread of large fires (Pausas et al. 2004, 2008). The capacity of this species to regenerate after a fire hinges on its canopy-stored seed bank; so, any fire interval shorter than its age to maturity (i.e., 10–20 years, Ne’eman et al. 2004) is likely to cause a regeneration failure (Daskalakou and Thanos 1996; Pausas et al. 2008). In contrast, hardwood species are mostly resprouters: they have the ability to regrow from dormant buds and belowground reserves after a fire, which promotes faster vegetation recovery and makes them less vulnerable to high fire frequencies (Pausas et al. 2004; Schelhaas et al. 2010). Resprouter species can thus be considered keystone species for fire-resilient forests (Puerta-Piñero et al. 2012). Furthermore, monospecific Aleppo pine stands have been shown to be highly sensitive to insect attacks (Maestre and Cortina 2004) and to reduce plant species richness and diversity in the understory (Chirino et al. 2006), whereas mixed pine–hardwood stands are shown to be less sensitive to pest outbreaks and herbivory (Jactel and Brockerhoff 2007), to potentially host greater biodiversity (Cavard et al. 2011), and to be more resilient to disturbances and changing environmental conditions for a number of ecosystem processes (Jactel et al. 2009; Yachi and Loreau 1999). Promoting mixed pine–hardwood stands is therefore increasingly advocated as a strategy to enhance forest resilience (Pausas et al. 2004; Keskitalo 2011).
Mixed stands can be created by introducing hardwood species into pine stands to overcome seed limitations, but the operation proves delicate in Mediterranean conditions where seedling survival in summer is a major demographic bottleneck. Successful seedling introduction hinges on selecting species adapted to local conditions (Padilla et al. 2009; Vallejo et al. 2012). Reducing tree density by thinning has also been shown to be a critical factor for seedling establishment in forest understory (Paquette et al. 2006). Thinning increases light availability in the understory but also affects the water balance in a more complex way (Aussenac 2000), with potentially important implications for seedling survival in water-limited areas. Forest managers need information on suitable management methods to enhance forest diversity and resilience; yet, few studies have investigated the effect of thinning on understory microclimate and seedling performance under Mediterranean conditions.
Here, we examined the effect of Aleppo pine thinning at three intensities in two different experimental sites—one in South-East Spain and one in South-East France. In each site, we assessed the effect of thinning on understory microclimate and the establishment (survival and growth) of six resprouter hardwood species. The applied objective was to help assess whether overstory thinning help hardwood species establishment for increasing biodiversity and resilience in Aleppo pine stands.
2 Material and methods
2.1 Experimental sites
Experiments were conducted at two sites in SE Spain and SE France (see map in Online Resource 1). In Spain, the experiment was located in the forest of La Hunde, Ayora, province of Valencia (hereafter “Ayora”) on a flat area at a mean altitude of 800 m (30° 7′ N; 1° 13′ W to 39° 6′ N; 1° 11′ W). In France, the experimental site was located at Saint-Mitre-les-Remparts in the Bouches-du-Rhône département (hereafter “St Mitre”) in a flat area adjacent to the Mediterranean Sea at a mean altitude of 130 m (43° 4′ N; 5° 0′ W). Both sites are covered by Aleppo pine forest forming closed stands aged 40–60 years old 32 m2/ha, originating from afforestation at Ayora and from natural colonization of abandoned land at St Mitre.
At Ayora, Aleppo pines were used to afforest former almond fields, and they are dominant in an area spanning over 1500 ha, with a sparse understory composed mainly of dwarf scrubs (Thymus sp.) and medium shrubs (Rosmarinus officinalis, Ulex parviflorus) and scattered adult Quercus ilex ballota. Soils are calcareous with a sandy-loam texture, stoniness in the range 27–49 %, and a mean depth of 35 cm. At St Mitre, the forest is located on old fields divided up by stone walls (“terraces”) over an area of about 150 ha surrounded by a mosaic of agricultural areas with sparse oak trees, shrublands, other Aleppo pine forests, and urban areas. The understory is composed of scattered Quercus ilex trees and a spatially heterogeneous shrub layer (main species, Quercus coccifera). Soils are calcareous with a sandy-loam texture, low stoniness, and a mean depth of 40 cm.
The climate is quite similar between the two sites. Historical records (1961–1990, Online Resource 2) show a dry season of 3 months and a mean temperature of 14 °C in both sites but a lower average annual rainfall at Ayora (480 mm) than at St Mitre (570 mm) mainly due to wetter autumns. During the experiment (2009–2014), annual rainfall at Ayora was 527 ± 48 mm with July–August rainfall of 14 ± 6 mm and annual rainfall at St Mitre was 561 ± 154 mm with July–August rainfall of 20 ± 3 mm except in 2011 (71 mm).
2.2 Thinning treatments and pine stand characteristics
At each site, three thinning treatments were tested: (i) unthinned, (ii) moderate thinning, and (iii) heavy thinning. At Ayora, the tinning treatments were applied in 2002 and removed about 50 and 75 % of initial basal area. Each treatment was replicated in three 30 m × 30 m plots (9 plots in total). At St Mitre, the tinning treatments were applied in 2006 and removed 30 % (moderate regime) and 60 % (heavy regime) of initial basal area. Each treatment was replicated in four 25 m × 25 m plots (12 plots in total). Before seedling introduction, each plot was inventoried by measuring the DBH of each tree >1.30 m high. The resulting stand characteristics for each treatment are shown in Table 1.
2.3 Selection and introduction of hardwood species
At each site, we selected 6 native species occurring in the surroundings (Table 2), with the exception of the thermophilous Ceratonia siliqua in France (subnatural and present at few locations along the Mediterranean coast). The two oak species are the main late-successional dominant species of hardwood forests: the evergreen oak Quercus ilex at both sites, and the deciduous oaks Quercus faginea at Ayora and Quercus pubescens at St Mitre. Seeds were collected in the region local to each experimental site at different locations with similar ecological conditions, using different trees for each species in order to account for intraspecific variability. Q. ilex and Q. pubescens at St Mitre were directly sown in November 2007 by introducing 3 acorns in 50 sowing points per plot. Other hardwood seedlings were cultivated in nurseries and transplanted into the field at 1 year old, in November 2009 at St Mitre and in November 2010 at Ayora. At Ayora, 15 seedlings per species and per plot were planted in holes dug by a backhoe. At St Mitre, 18 seedlings per species and per plot were planted in holes dug manually. Plots were fenced to avoid predation by large herbivores. Herbivory by insects may still have occurred, but although not specifically recorded, we did not notice important events and assume that herbivory pressure was similar between thinning treatments.
2.4 Monitoring of environmental factors
Light transmission, soil moisture, air temperature, and air humidity were monitored at both sites. Solar photosynthetically active radiation (PAR) transmission was calculated in each plot as the ratio of photosynthetic photon flux density (PPFD, μmol m−2 s−1) in the plot to the PPFD at a nearby open site in July. At Ayora, 10 PPFD measures were taken in each plot and in the open every 3 h from 6 a.m. to 6 p.m., using a ceptometer (Sunfleck, Decagon devices, USA). At St Mitre, PPFD was recorded every minute for 24 h using 5 sensors per plot (SKP 215, Skye Instruments, UK).
Soil water content was measured at two depths: top layer (0–10 cm) and at 30-cm depth. At Ayora, soil water content in the top layer was recorded on a monthly basis using 7 TDR probes per plot (TDR100, Campbell Scientific) placed in randomly selected plantation holes. Soil moisture at 30-cm depth was simultaneously recorded on a subsample of 3 randomly selected plantation holes per plot using an HS-10 volumetric water content sensor (ProCheck, Decagon Devices, USA). At St Mitre, soil moisture in the top layer was measured monthly with a portable TDR probe (Wet2, Delta-T Devices, UK) at 9–15 measurement points, and soil moisture at 30-cm depth was recorded hourly by 12 TDR probes per treatment distributed in two randomly selected plots (EC-5, Decagon Device). Measurements were taken in two consecutive years in each site, i.e., 2011–2012 at Ayora and 2013–2014 at St Mitre.
Air temperature and humidity were monitored hourly using 3–5 sensors per treatment, distributed in the same plots as the TDR probes. Sensors (HOBO sensors at Ayora and Hygrochron iButton DS1923 sensors at St Mitre) were installed at an aboveground height of about 30 cm in small shelters to protect them from direct radiation and rainfall. From temperature and air humidity, we calculated the vapor pressure deficit (VPD), which is closely related to plant evapotranspiration (FAO 1998). The data was then used to calculate daily mean, maximum and minimum temperature, and VPD.
2.5 Seedlings and understory vegetation monitoring
Each seedlings was individually tagged. Survivorship, basal diameter, and height were measured yearly. For oaks sown in St Mitre, all emerged acorns were measured, and the mean of the sowing-point seedling dimensions was used to avoid pseudoreplication. Growth measurements were used to compile a relative growth rate (RGR) in basal diameter and height for 3-year-old seedlings, as follows (Hoffmann and Poorter 2002):
where X i is the performance indicator (height or diameter) at the last measurement date t i and X 0 is the same indicator at the first measurement date t 0 (first year after sowing for Quercus species sown at St Mitre, outplanting for other species).
Three years after seedling introduction, understory shrub and herb covers were visually assessed, and shrub height was recorded using 3 to 10 transects per plot.
2.6 Data analysis
As the two site conditions differed on several factors such as history, species introduced, and intensity of thinning treatments, the statistical analyses were conducted separately for each site. Effects of thinning on light transmission and mean seasonal soil water content were tested by one-way ANOVA. Effects of thinning on other environmental factors were analyzed using linear mixed models, with treatment and date as fixed factor and measurement sites (probes) as random factor. Thinning treatments and species differences in survival over time were tested by comparing Kaplan-Meier estimates of the survival function (Kaplan and Meier 1958) with a Mantel-Cox log-rank test. Effect of treatment and species identity on final seedling RGR was tested using two-way ANOVA after first transforming the variables (if necessary) to satisfy the conditions of normality and homoscedasticity of residuals. Post hoc Tukey tests evaluated between-treatment differences for each species. All statistical analyses were performed using R software (3.1.0).
3.1 Understory microclimate and vegetation development
At both sites, mean light transmission, maximum daily temperature, and VPD increased with canopy openness (Table 3). Maximum PPFD in the open was about 2300 μmol m−2 s−1 at both sites. Light transmission reached higher values at Ayora but decreased with basal area as a negative exponential relationship and in a consistent way between the two sites (Online Resource 3). The increase in maximum temperature and VPD with canopy openness was particularly pronounced in summer, where temperature increase reached 13 % increase in both sites and VPD increase reached 14 % (Ayora) to 40 % (St Mitre) in the heavy thinning treatment.
Thinning did not affect soil water content in the upper layer in either site (Online Resource 4). In the deeper layer, soil water content was higher in the heavy thinning treatment at Ayora (p = 0.01, Fig. 1). This difference persisted all year long, although it was higher in the rainy seasons (winter and spring, +23 %) than in the dry seasons (summer and early autumn, +17 %). At St Mitre, between-treatment differences were not significant (p = 0.5), but there was a strong date × treatment interaction (p < 0.001, Fig. 1): in the rainy seasons, soil water content tended to be higher in the thinned treatments while in summer, soil water content decreased sharply and tended to be lower in the heavy thinning treatments.
Canopy opening induced the development of spontaneous vegetation in the understory at both sites, but with different compositions (Table 3). Herb cover increased in response to thinning at Ayora, from 0.3 % in the unthinned plots to 21.4 % in heavily thinned plots, whereas at St Mitre, herbs were only found on a few thinned plots and remained very scarce, accounting for less than 1 % of soil cover. At St Mitre, shrub cover and height increased progressively with thinning intensity, whereas at Ayora shrub, cover was only higher under the moderate thinning treatment.
3.2 Seedling survival and growth
Seedling survival rate was influenced by thinning treatment (log-rank = 13.2, p < 0.01 at Ayora and log-rank = 59.7, p < 0.001 at St Mitre), with few differences between the moderate and heavy thinning treatments. Seedling survival ranged from 22 to 99 % at St Mitre and from 52 to 100 % at Ayora (Fig. 2). At Ayora, survival of half of the species was decreased under thinning treatments. However, the decrease in survival rate never exceeded 23 % even for the most severely affected species which still showed high survival rates in the most open treatments (minimum 77 ± 6 % for R.alaternus). In contrast, at St Mitre, thinning had a positive effect on the survival of all species (except F. ornus, with survival rates remaining very high 97.2–98.6 %). Thinning had particularly strong positive effects on A. unedo and Q. pubescens, leading to 3-fold and 2-fold increases in survival rates, respectively.
Survival was also affected by species identity in both sites (log-rank = 74.8, p < 0.001 at Ayora, log-rank = 189.0, p < 0.001 at St Mitre). The species with the lowest survival rates were the two deciduous trees Q. faginea and A. granatense at Ayora and the evergreen A. unedo and C. siliqua at St Mitre.
Thinning had a positive effect on stem diameter growth for all species at both sites (Table 4, Fig. 2). Thinning also strongly improved all-species height growth at St Mitre, whereas at Ayora, thinning decreased the height growth of two species: Q. faginea and R. alaternus. The best growing species in terms of diameter were R. alaternus and A. unedo at Ayora and Q. ilex at St Mitre. At Ayora, thinning changed the pattern of species responses in terms of height growth. The best performing species was R. alaternus in the unthinned treatment and F. ornus and A. granatense in the thinning treatments. At St Mitre, F. ornus and S. domestica showed particularly dynamic height growth, whereas C. siliqua showed negative growth rates in all treatments as well as A. unedo in unthinned treatments. This pattern reflected a destruction of aboveground biomass of the two latter species followed by resprouting during the experiment. C. siliqua is known to be frost-sensitive, and the bulk of its biomass destruction occurred after an extreme frostwave. However, even in this case, thinning improved seedling growth after resprouting.
Mixed pine–hardwood forests are expected to be more resilient to disturbances than monospecific pine stands (Jactel et al. 2009; Vallejo et al. 2006), particularly to allow quicker vegetation recovery after frequent large fires (Puerta-Piñero et al. 2012). Favoring the establishment of resprouting hardwood seedlings under Aleppo pine stands is thus recommended, but no clear management methods have yet been established. The aim here was to study how active management by overstory thinning could modify environmental factors and influence the seedling establishment of various resprouting hardwood species.
4.1 Thinning effect on understory microclimate
Our results showed a buffering effect on air temperature and VPD that increased with tree basal area. This effect was more pronounced during the drier season, as also found by Rambo and North (2009), which may prove important for seedling survival in this critical period. Heavy thinning increased soil moisture only in wet seasons at St Mitre but even during summer at Ayora. Although time elapsed between thinning and soil measurement was longer at Ayora than at St Mitre, this lag probably had little effect on the observed trends. In fact, contrary to what was observed at Ayora, long-term studies (e.g., Gray et al. 2002) have found an absence of differences in soil moisture between thinned and unthinned treatments after several years due to vegetation development in thinned stands. Other studies diverge on the effects of tree thinning on soil water content, with some reporting positive outcomes (Bellot et al. 2004; Bréda et al. 1995; Rodriguez-Calcerrada et al. 2008) but others reporting negative outcomes (Primicia et al. 2012; Simonin et al. 2007). This divergence illustrates the fact that tree cover has diverse impacts on water balance: trees intercept rainfall and consume soil water, but also reduce understory evapotranspiration (Aussenac 2000). Understory vegetation is known to account for a substantial share of total pine stand evapotranspiration, in particular in dry seasons due to pine stomatal closure (Simonin et al. 2007). Thus, differences between sites may be linked to differences in understory vegetation: tall shrubs at St Mitre probably consumed more water at 30-cm depth in summer than the herbs and dwarf shrubs at Ayora.
4.2 Thinning effect on seedling survival and growth
Thinning improved stem diameter growth of seedlings at both sites, but had site-specific effects on seedling survival and height growth.
The higher mortality in heavily thinned stands at Ayora revealed that these stands were more stressful for seedlings despite their higher summer soil moisture. Soil water content is not always related to water availability for seedlings, which is strongly dependent on root development (Padilla and Pugnaire 2007). Moreover, higher evaporative demand, temperatures, and light levels in thinned plots can increase drought stress and directly damage seedling tissues and the photosynthetic machinery (Chaves et al. 2002; Valladares 2004), which probably overrode the benefits of higher soil moisture. Seedlings were more likely to die in heavily thinned stands at Ayora due to more stressful conditions in summer, but the surviving seedlings grew better in diameter due to the higher light availability during the growing season. Such life-stage conflicts of canopy shelter effects on seedling survival and growth are frequently reported in the Mediterranean (e.g., Caldeira et al. 2014; Gómez-Aparicio et al. 2008; Marañón et al. 2004; Soliveres et al. 2010). Furthermore, height growth is the result of a balance between growth ability and elongation in response to changes in light quantity and quality (red/far-red ratio; Franklin 2008), which probably explains the species-dependent effect of thinning on height growth at Ayora.
The conflict between survival and growth did not occur at St Mitre, where thinning strongly stimulated survival, diameter, and height growth. Light transmission in dense stands was lower at St Mitre than at Ayora. Although this difference was small (5 %), at low light levels, a small change in light availability can trigger a large drop in survival rates (e.g., Sánchez-Gómez et al. 2006), which may explain the low survival of several species under dense stands at St Mitre. Thinning thus increased survival and growth despite slightly lower summer-season soil moisture, as also found by Rodriguez-Calcerrada et al. (2010) in central Spain. The higher light availability in thinned stands thus fostered better overall above-ground seedling development (in both diameter and height) and probably also below-ground development, enabling seedlings to better cope with summer drought. In this case, the positive effect of light availability was not cancelled out by the parallel increase in heat stress and evaporative demand like at Ayora, almost certainly because the summer conditions in the heavy thinning treatments were less stressful at St Mitre than at Ayora, as shown by the lower light transmission (38 vs 63 %), maximum temperature (34.8 vs 36.0 °C) and VPD (3.9 vs 4.9 kPa) values. In Rodriguez-Calcerrada et al. (2010), the highest light transmission was a similar 35 %, and conditions may not have been stressful enough to trigger decreased survival. Indeed, the interplay between light and water stress is a complex issue, and it has been suggested that drought is more severe for plants at both low and high light levels yet ameliorated at intermediate light levels (Holmgren et al. 2012). Our results thus suggest that intermediate pine densities are the most favorable for hardwood seedling establishment. This adds support to results by Gómez-Aparicio et al. (2009) in an observational study of Q. ilex recruitment under Aleppo pine woodlands, and by Paquette et al. (2006) in a meta-analysis including contrasted climatic areas. In water-limited Mediterranean areas, this result seems to be driven by a trade-off between light availability and abiotic summer conditions determining mortality rates.
4.3 Understory vegetation development and potential impact on seedling establishment
Thinning fostered the development of different types of understory vegetation, mostly herbs and dwarf shrubs at Ayora and tall shrubs at St Mitre, which may have partly shaped the thinning effects (Paquette et al. 2006). Understory vegetation can have a distinct impact on seedling establishment depending on morphology, growth rates, and/or ability to deplete resources (Balandier et al. 2006). Herbaceous species present in thinned plots at Ayora are known to be highly competitive with young seedlings (e.g., Caldeira et al. 2014; Cuesta et al. 2010), while at St Mitre, the understory of thinned plots was mainly colonized by shrubs that are often involved in positive interactions in Mediterranean settings (Castro et al. 2004). There has been little research into shrub effects in Mediterranean understory, but the evidence suggests that shrubs may have positive effects by mitigating the increase in extreme temperatures and creating lateral shading which favors height growth (Prévosto et al. 2011). Spontaneous vegetation development is difficult to foresee and depends on landscape context and seed sources, but this aspect warrants further study and should be taken into account when designing a thinning strategy.
4.4 Species selection to increase forest diversity and resilience
The outcome of plant–plant interactions can vary widely with target species identity and strategy (e.g., Liancourt et al. 2005). In this study, all target species at each site responded to thinning in the same direction but with different magnitudes, probably reflecting different stress tolerances and competitive abilities. For instance, light-demanding drought-tolerant species probably benefited more from post-thinning canopy opening, but the fact is that the precise ecological requirements of many hardwood species used in this study are still largely unknown. The thermophilous species (C. siliqua) used at St Mitre performed badly in all treatments, probably due to its frost sensitivity, which highlights how selecting species adapted to expected future climate conditions remains a very risky strategy (Lindner et al. 2008). Between sites, no common pattern of species performance according to life-form or leaf habit (as described in Table 2) emerged. For instance, at Ayora, the best-performing species were evergreen drought-tolerant shrubs, R. alaternus and A. unedo, while at St Mitre, A. unedo posted some of the poorest survival and growth rates. Deciduous species have been reported as intolerant to high irradiance (Gómez-Aparicio et al. 2006). Here, Q. faginea growth was indeed strongly reduced under heavy thinning treatments at Ayora, but other deciduous species showed intermediate-to-good performances. Although these species may be affected by higher irradiances, under moderate pine cover, they seem to represent a suitable opportunity for pine forest diversification. Their different leaf habit promotes a higher functional diversity, which has been shown to be of interest for forest resilience (Pedro et al. 2015). Species performances were higher and differences between species less important under moderate pine cover than under very dense or very light cover, which allows a wider range for species choice. In addition to resprouting ability, other properties may be key factors for species selection, such as valuable wood (F. ornus, S. domestica), fleshy fruits favoring bird diversity (A. unedo, S. domestica), or conservation of an endangered species (A. granatense).
Mixing Aleppo pine stands with hardwood species require appropriate management of the overstory layer to enhance hardwood seedling establishment. Thinning is necessary to release light limitation in dense pine stands, but excessive thinning may aggravate the already tough summer conditions and reduce the likelihood of seedling survival, particularly if drought events come frequently. Our results suggest that intermediate pine densities of about 15–20 m2/ha offer the most suitable conditions to boost introduced seedling growth and foster high later survival, although longer-term studies are needed to confirm the potential of this management strategy to create mixed stands. Several native resprouter species can be introduced under intermediate pine densities which should allow for diversification and increased resilience of Aleppo pine stands. However, site-specific climate conditions and interactions with understory herb and shrub layers can influence the effects of thinning on microclimate and seedling establishment, and thus warrant further investigation.
Aussenac G (2000) Interactions between forest stands and microclimate: ecophysiological aspects and consequences for silviculture. Ann For Sci 57:287–301
Balandier P, Collet C, Miller JH, Reynolds PE, Zedaker SM (2006) Designing forest vegetation management strategies based on the mechanisms and dynamics of crop tree competition by neighbouring vegetation. Forestry 79:3–27. doi:10.1093/forestry/cpi056
Barbero M, Bonin G, Loisel R, Quézel P (1990) Changes and disturbances of forest ecosystems caused by human activities in the western part of the Mediterranean Basin. Vegetatio 87:151–173. doi:10.1007/BF00042952
Bellot J, Maestre FT, Chirino E, Hernández N, de Urbina JO (2004) Afforestation with Pinus halepensis reduces native shrub performance in a Mediterranean semiarid area. Acta Oecol 25:7–15. doi:10.1016/j.actao.2003.10.001
Bréda N, Granier A, Aussenac G (1995) Effects of thinning on soil and tree water relations, transpiration and growth in an oak forest (Quercus petraea (Matt.) Liebl.). Tree Physiol 15:295–306. doi:10.1093/treephys/15.5.295
Caldeira MC, Ibáñez I, Nogueira C, Bugalho MN, Lecomte X, Moreira A, Pereira JS (2014) Direct and indirect effects of tree canopy facilitation in the recruitment of Mediterranean oaks. J Appl Ecol 51:349–358. doi:10.1111/1365-2664.12189
Castro J, Zamora R, Hódar JA, Gómez JM, Gómez-Aparicio L (2004) Benefits of using shrubs as nurse plants for reforestation in Mediterranean mountains: a 4-year study. Restor Ecol 12:352–358. doi:10.1111/j.1061-2971.2004.0316.x
Cavard X, Macdonald SE, Bergeron Y, Chen HYH (2011) Importance of mixedwoods for biodiversity conservation: evidence for understory plants, songbirds, soil fauna, and ectomycorrhizae in northern forests. Environ Rev 19:142–161. doi:10.1139/a11-004
Chaves MM, Pereira JS, Maroco J, Rodrigues ML, Ricardo CPP, Osório ML, Carvalho I, Faria T, Pinheiro C (2002) How plants cope with water stress in the field? Photosynthesis and growth. Ann Bot 89:907–916. doi:10.1093/aob/mcf105
Chirino E, Bonet A, Bellot J, Sánchez JR (2006) Effects of 30-year-old Aleppo pine plantations on runoff, soil erosion, and plant diversity in a semi-arid landscape in south eastern Spain. Catena 65:19–29. doi:10.1016/j.catena.2005.09.003
Cuesta B, Villar-Salvador P, Puértolas J, Rey Benayas JM, Michalet R (2010) Facilitation of Quercus ilex in Mediterranean shrubland is explained by both direct and indirect interactions mediated by herbs. J Ecol 98:687–696. doi:10.1111/j.1365-2745.2010.01655.x
Daskalakou E, Thanos C (1996) Aleppo pine (Pinus Halepensis) postfire regeneration: the role of canopy and soil seed banks. Int J Wildland Fire 6:59–66
FAO (1998) Meteorological data, in: crop evapotranspiration - guidelines for computing crop water requirements, FAO irrigation and drainage papers. Food and Agriculture Organization of the United Nations, Rome
Franklin KA (2008) Shade avoidance. New Phytol 179:930–944. doi:10.1111/j.1469-8137.2008.02507.x
Gómez-Aparicio L, Valladares F, Zamora R (2006) Differential light responses of Mediterranean tree saplings: linking ecophysiology with regeneration niche in four co-occurring species. Tree Physiol 26:947–958
Gómez-Aparicio L, Pérez-Ramos IM, Mendoza I, Matías L, Quero JL, Castro J, Zamora R, Marañón T (2008) Oak seedling survival and growth along resource gradients in Mediterranean forests: implications for regeneration in current and future environmental scenarios. Oikos 117:1683–1699. doi:10.1111/j.1600-0706.2008.16814.x
Gómez-Aparicio L, Zavala MA, Bonet FJ, Zamora R (2009) Are pine plantations valid tools for restoring Mediterranean forests? An assessment along abiotic and biotic gradients. Ecol Appl 19:2124–2141
Gray AN, Spies TA, Easter MJ (2002) Microclimatic and soil moisture responses to gap formation in coastal Douglas-fir forests. Can J For Res 32:332–343. doi:10.1139/x01-200
Hoffmann WA, Poorter H (2002) Avoiding bias in calculations of relative growth rate. Ann Bot 90:37–42. doi:10.1093/aob/mcf140
Holmgren M, Gómez-Aparicio L, Quero JL, Valladares F (2012) Non-linear effects of drought under shade: reconciling physiological and ecological models in plant communities. Oecologia 169:293–305. doi:10.1007/s00442-011-2196-5
Jactel H, Brockerhoff EG (2007) Tree diversity reduces herbivory by forest insects. Ecol Lett 10:835–848. doi:10.1111/j.1461-0248.2007.01073.x
Jactel H, Nicoll BC, Branco M, Gonzalez-Olabarria JR, Grodzki W, Långström B, Moreira F, Netherer S, Orazio C, Piou D, Santos H, Schelhaas MJ, Tojic K, Vodde F (2009) The influences of forest stand management on biotic and abiotic risks of damage. Ann For Sci 66:701–701. doi:10.1051/forest/2009054
Kaplan EL, Meier P (1958) Nonparametric estimation from incomplete observations. J Am Stat Assoc 53:457–481. doi:10.1080/01621459.1958.10501452
Keskitalo ECH (2011) How can forest management adapt to climate change? Possibilities in different forestry systems. Forests 2:415–430
Kovats RS, Valentini R, Brower LM, Georgopoulou E, Jacob D, Martin E, Rounsevell M, Soussana J-F (2014). Europe, in: climate change 2014: impacts, adaptation, and vulnerability. Part B: regional aspects. Contribution of Working Group II to the Fifth Assessment Report of the Intergovernmental Panel on Climate Change. Barros V.R., C.B. Field, D.J. Dokken, M.D. Mastrandrea, K.J. Mach, T.E. Bilir, M. Chatterjee, K.L. Ebi, Y.O. Estrada, R.C. Genova, B. Girma, E.S. Kissel, A.N. Levy, S. MacCracken, P.R. Mastrandrea and L.L. White, Cambridge, United Kingdom and New York, NY, USA, pp. 1267–1326.
Liancourt P, Callaway RM, Michalet R (2005) Stress tolerance and competitive-response ability determine the outcome of biotic interactions. Ecology 86:1611–1618. doi:10.2307/3450786
Lindner M, Garcia-Gonzalo J, Kolström M, Green T, Reguera R, Maroschek M, Seidl R, Lexer MJ, Netherer S, Schopf A, Kremer A, Delzon S, Barbati A, Marchetti M, Corona P (2008) Impacts of climate change on European forests and options for adaptation (Report to the European Commission Directorate-General for Agriculture and Rural Development)
Maestre FT, Cortina J (2004) Are Pinus halepensis plantations useful as a restoration tool in semiarid Mediterranean areas? For Ecol Manag 198:303–317. doi:10.1016/j.foreco.2004.05.040
Marañón T, Zamora R, Villar R, Zavala MA, Quero JL, Pérez-Ramos IM, Mendoza I, Castro J (2004) Regeneration of tree species and restoration under contrasted Mediterranean habitats: field and glasshouse experiments. Int J Ecol Environ Sci 30:187–196
Moriondo M, Good P, Durao R, Bindi M, Giannakopoulos C, Corte Real J (2006) Potential impact of climate change on fire risk in the Mediterranean area. Clim Res 31:85–95. doi:10.3354/cr031085
Ne’eman G, Goubitz S, Nathan R (2004) Reproductive traits of Pinus halepensis in the light of fire - a critical review. Plant Ecol 171:69–79. doi:10.1023/B:VEGE.0000029380.04821.99
Ortuño F (1990) El plan para la repoblación forestal de España del año 1939. Análisis y comentarios. Ecología Fuera Ser 1:373–392
Padilla FM, Pugnaire FI (2007) Rooting depth and soil moisture control Mediterranean woody seedling survival during drought. Funct Ecol 21:489–495. doi:10.1111/j.1365-2435.2007.01267.x
Padilla FM, Ortega R, Sánchez J, Pugnaire FI (2009) Rethinking species selection for restoration of arid shrublands. Basic Appl Ecol 10:640–647. doi:10.1016/j.baae.2009.03.003
Paquette A, Bouchard A, Cogliastro A (2006) Survival and growth of under-planted trees: a meta-analysis across four biomes. Ecol Appl 16:1575–1589. doi:10.2307/40062023
Pausas JG, Bladé C, Valdecantos A, Seva JP, Fuentes D, Alloza JA, Vilagrosa A, Bautista S, Cortina J, Vallejo R (2004) Pines and oaks in the restoration of Mediterranean landscapes of Spain: new perspectives for an old practice—a review. Plant Ecol 171:209–220
Pausas JG, Llovet J, Rodrigo A, Vallejo R (2008) Are wildfires a disaster in the Mediterranean basin? - A review. Int J Wildland Fire 17:713–723. doi:10.1071/WF07151
Pedro MS, Rammer W, Seidl R (2015) Tree species diversity mitigates disturbance impacts on the forest carbon cycle. Oecologia 177:619–630. doi:10.1007/s00442-014-3150-0
Prévosto B, Monnier Y, Ripert C, Fernandez C (2011) Diversification of Pinus halepensis forests by sowing Quercus ilex and Quercus pubescens acorns: testing the effects of different vegetation and soil treatments. Eur J For Res 130:67–76. doi:10.1007/s10342-010-0396-x
Primicia I, Camarero JJ, Imbert JB, Castillo FJ (2012) Effects of thinning and canopy type on growth dynamics of Pinus sylvestris: inter-annual variations and intra-annual interactions with microclimate. Eur J For Res 132:121–135. doi:10.1007/s10342-012-0662-1
Puerta-Piñero C, Brotons L, Coll L, González-Olabarría JR (2012) Valuing acorn dispersal and resprouting capacity ecological functions to ensure Mediterranean forest resilience after fire. Eur J For Res 131:835–844. doi:10.1007/s10342-011-0557-6
Rambo TR, North MP (2009) Canopy microclimate response to pattern and density of thinning in a Sierra Nevada forest. For Ecol Manag 257:435–442. doi:10.1016/j.foreco.2008.09.029
Rodriguez-Calcerrada J, Mutke S, Alonso J, Gil L, Pardos JA, Aranda I (2008) Influence of overstory density on understory light, soil moisture, and survival of two underplanted oak species in a Mediterranean montane Scots pine forest. For Syst 17:31–38. doi:10.5424/1021
Rodriguez-Calcerrada J, Cano FJ, Valbuena-Carabana M, Gil L, Aranda I (2010) Functional performance of oak seedlings naturally regenerated across microhabitats of distinct overstorey canopy closure. New For 39:245–259. doi:10.1007/s11056-009-9168-1
Sánchez-Gómez D, Valladares F, Zavala MA (2006) Performance of seedlings of Mediterranean woody species under experimental gradients of irradiance and water availability: trade-offs and evidence for niche differentiation. New Phytol 170:795–805. doi:10.2307/3694414
Schelhaas M-J, Hengeveld G, Moriondo M, Reinds GJ, Kundzewicz ZW, ter Maat H, Bindi M (2010) Assessing risk and adaptation options to fires and windstorms in European forestry. Mitig Adapt Strat Glob Chang 15:681–701. doi:10.1007/s11027-010-9243-0
Simonin K, Kolb TE, Montes-Helu M, Koch GW (2007) The influence of thinning on components of stand water balance in a ponderosa pine forest stand during and after extreme drought. Agric For Meteorol 143:266–276. doi:10.1016/j.agrformet.2007.01.003
Soliveres S, DeSoto L, Maestre FT, Olano JM (2010) Spatio-temporal heterogeneity in abiotic factors modulate multiple ontogenetic shifts between competition and facilitation. Perspect Plant Ecol Evol 12:227–234. doi:10.1016/j.ppees.2010.02.003
Valladares F (2004) Photoinhibition and drought in Mediterranean woody saplings: scaling effects and interactions in sun and shade phenotypes. J Exp Bot 56:483–494. doi:10.1093/jxb/eri037
Vallejo VR, Aronson J, Pausas JG, Cortina J (2006) Restoration of Mediterranean woodlands, in: restoration ecology: the new frontier. Van Andel J., Aronson J, Oxford, pp 193–209
Vallejo VR, Smanis A, Chirino E, Fuentes D, Valdecantos A, Vilagrosa A (2012) Perspectives in dryland restoration: approaches for climate change adaptation. New For 43:561–579. doi:10.1007/s11056-012-9325-9
Yachi S, Loreau M (1999) Biodiversity and ecosystem productivity in a fluctuating environment: the insurance hypothesis. PNAS 96:1463–1468. doi:10.1073/pnas.96.4.1463
The authors thank Christian Ripert, Roland Estève, Jean-Michel Lopez, and Fabien Guerra (Irstea, UR EMAX) for their help with field work at St Mitre. E. Chirino thanks the Prometheus Project (SENESCYT, Ecuador) for funding his grant.
This work was supported by the project FUME (FP7-Environment, GA. 243888). Irstea also received funds from the Region Provence-Alpes-Côte-d’Azur and the Ministry of Ecology (MEDDE–DEB). CEAM was also supported by the projects SURVIVE (CGL-2011-30531-CO2-02), Consolider-GRACCIE (CTM2014-59111-REDC) and receive support from the Generalitat Valenciana.
Handling Editor: Lluis Coll
Contribution of the co-authors
AV, EC, VRV, and BP were involved in the design of the experiment. All authors participated to field data collection and writing the manuscript. JG wrote the first version of the manuscript and, together with AV, analyzed the data. VRV in Spain and BP in France designed and supervised the experiment implementation and coordinated the work.
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Gavinet, J., Vilagrosa, A., Chirino, E. et al. Hardwood seedling establishment below Aleppo pine depends on thinning intensity in two Mediterranean sites. Annals of Forest Science 72, 999–1008 (2015). https://doi.org/10.1007/s13595-015-0495-4