Many wildland fires affect forests and wildlands in Spain in last years like in other South Europe countries (Greece, Portugal, Italy or France) or elsewhere (Pereira et al., 2011). Some of them had a severe fire behavior and burned large areas, causing economic and environmental losses (Cardil & Molina, 2013; Cardil et al., 2014). However, in the highest areas of the Spanish Pyrenees where Pinus uncinata Ram. (PU) areas can be found (Serrada et al., 2008; Stähli et al., 2006; Conedera & Tinner, 2004) few large, severe wildland fires occurred yet. Most of the PU forests are located in the Pyrenees, where the species is dominant at elevations from 1800 to 2500 m a.s.l. usually forming low-density stands (Galván et al., 2014). Detailed information about PU specie in Spain can be found in Blanco et al. (2013).

Fire is usually relevant to maintain pine stand processes, but it is also the most significant threat to forest stands in the Mediterranean Basin when fire regime changes (Barbéro et al., 1998; Pausas & Fernandez-Muñoz, 2012). Forestry species (or populations) are usually adapted to a specific fire regime in each location. Fire ecology is fairly well known in many major forestry species: Fire ecology of most European pines species have been studied (Fernandes et al., 2008; Fernandes & Rigolot, 2007). However, few references can be found and there is not much knowledge about the fire ecology of Pinus uncinata Ram. Lacking of the specific knowledge on fire ecology for PU does not allow the best possible management of those stands (i.e., best fuel management). Few records of wildland fire occurrence are explicit in EGIF database (General Statistics on Wildland Fires) and most of them display small fire events in PU areas. Additionally, climate change trends might favor fire occurrence and a more extreme fire behavior (Cardil et al., 2013; Cardil et al., 2015; Gianakopoulus et al., 2009).

Several severe wildfires occurred in the winter season in the Central Pyrenees (Huesca and Lleida provinces). These fires were very intense with high rate of spread and large flame length due to the physiological drought of the vegetation, the lack of snow cover, and the steep slopes. Little knowledge is in the literature about fire tolerance of PU and the fire effects in the species survival or enhances productions of seeds. This work is a first approximation to assess the effect of fire intensity, fire severity and influencing factors on PU mortality after a wildfire.

PU mortality was very different according to fire intensity (p-value<0.001; logistic regression; Table 1). PU mortality was not high under low and moderate intensity fire events (5 % in low fire intensity and between 15 and 30 % in moderate fire intensity). In contrast, in high fire intensity areas, mortality rate was very high (more than 90 % of trees died two years after the fire). According to the logistic regression, the probabilities of tree mortality in medium and high fire intensity areas were respectively 8.08 (1.26 - 14.35; confidence level: 95 %) and 269.5 (125.93 - 576.74; confidence level: 95 %) times higher than those trees in low intensity areas. Comparing medium and high fire intensity areas, those trees located in high intensity areas had a probability of mortality 33.32 (18.98 – 58.49; confidence level: 95 %) times higher than in medium fire intensity areas.

In plots located in medium fire line intensity areas, two months after the fire (3 April 2012), some trees seemed to be in a critical state (20 % trees with more than 80 % of the crown scorched). However, 6 months later (20 October 2012), the average scorched crown decreased (Table 2) and new shoots (green branches) were present. Therefore, most trees increased there green foliage in this period. More than 2 years later (November 2014), around 30% of trees had died. We have studied the relationship between fire severity and PU mortality considering several variables. Both the percentage of scorched crown volume and scorched height were statically influencing variables on tree mortality (p-value<0.001; logistic regression; Table 1). The percentage of scorched crown was also an influencing factor regarding the probability of mortality in Pinus halepensis Mill. and Pinus pinea L. forests (Rigolot, 2004). The most effective indicator of crown injury appears to be the proportion of the crown scorched or killed by fire (Ryan et al. 1988, Ryan & Reinhardt, 1988). Comparing trees having a crown scorched over 66% of its volume versus less scorched trees, we found that the probability of tree mortality was 48 times higher in the most scorched crowns (4.66 – 1,263.21; confidence level: 95 %; p-value<0.01). Mean scorched crown volume was 72% in dead trees versus 40% in live trees. Not significant relationships were found in terms of tree mortality in medium fireline intensity plots in relation to the tree height (p-value=0.11), diameter (p-value=0.75), bark thickness (p-value=0.97), minimum scorched height and maximum bark char height around the whole trunk perimeter (p-value=0.98). Therefore, in low and moderate intensity levels, we can deduce that PU individuals did survive as well developed individuals (adult trees). This is a resistant strategy (i.e., after the disturbance, a tree persisted as adult individual) to low or moderate fireline intensity. By contrast, in the areas with high fire intensity, fire burned crowns (either as passive or active crown fire) and mortality was very high (i.e., 92.4%, 231 dead, 19 alive). Therefore, it seems that the species is not well adapted to high fireline intensity: It is clear that PU lacks of adaptations to intense fires as other species like Pinus halepensis (serotines cones), Pinus canariensis (resprouting) or Quercus suber (bark thickness and resprouting) (Fernandes et al., 2008; Pausas, 1997). However, it could regenerate in the burned area from seeds from few individuals that survive inside the burned stand or from unburned islands or from PU populations outside the fire perimeter. This effect could be key because of it is a clearly stress tolerant species to cold, blizzards, short growing seasons. In short, it is the fittest species to this stress dominated habitat.

There is still a lot of knowledge to be gain about fire ecology of PU. This understanding is critical to properly manage these forests and also to assess implications of climate change and changes in fire regime (Fernandes et al., 2013). Wildland fires with an intense fire behavior did not occur frequently in the past. Meteorological and climatic conditions could change this in the near future, decreasing the vitality of trees and providing more frequent and extreme wildland fires in the Pyrenees, causing an environmental damage if forest managers do not work on minimizing fuel load with prescribed burning and its subrogates.

We understand that it is possible to plan prescribed fires in PU areas due to the tolerance of the species under low and moderate fireline intensity fires. We can monitor fire behavior with low and medium fire line intensity. Additionally, prescribed burns allow treated surfaces and, therefore, we have a chance to control this emerging phenomenon of high intensity wildfires in high mountains (Conedera & Tinner, 2004; Allen et al., 2010).

Few references can be found about fire ecology of Pinus uncinata Ram. This work is a first scientific approximation to assess the effect of fire intensity and fire severity on PU mortality after a wildland fire. PU mortality were very different according to fire intensity. The species is tolerant to low and moderate fireline intensity fires but tree mortality is very high in high fireline intensity fires. Both the percentage of scorched crown volume and scorched height were statically influencing variables on tree mortality.