Materials and Methods

Study site: This research was carried out from December 2009 to August 2011 at Las Cruces Biological Station (LCBS 8°47’07’’ N - 82°57’32’’ W) and the community of Agua Buena de Coto Brus (8°44’42’’ N - 82°56’53’’ W) in Southeastern Costa Rica. The site corresponds to a tropical montane moist forest (^{Holdridge, 1978}), with an annual rainfall of 3 500 mm and an average annual temperature of 20 °C. The dry season goes from December to March. The site is located between 1 000 and 1 300 masl. Soils are dominated by Andisols, which are formed by volcanic deposits and weathering by acid rain. Andisols are rejuvenated and enriched by andesitic volcanic ash additions and have relatively moderate fertility. However, some studies indicate that in this area the soils are dominated by plagioclases over orthoclases, which create a pronounced Potassium deficiency (^{Henríquez & Bertsch, 1994}; ^{Alvarado & Mata 2015}). The region was largely forested until approximately 1950, when most of the land was converted into coffee plantations. However, the drop in the international price of coffee led to the replacement of coffee plantations to other land uses (mainly pastures) or their abandonment, which allowed natural regeneration (^{Rickert, 2005}). Currently, the landscape is largely deforested and characterized by a mosaic of pastures, agriculture and small remnants of secondary forests concentrated along steep slope conditions and near rivers (^{Zahawi, Duran, & Kormann, 2015}). LCBS maintains the largest remaining fragment of primary forest in the immediate region. Less than 27 % of the area surrounding LCBS remains forested (^{Daily, Ehrlich, & Sánchez- Azofeifa, 2001}). Due to the high levels of deforestation and land erosion, most of the conservation efforts are focused in the restoration of degraded lands (^{Holl et al., 2011}).

Study species: We chose five native tree species with different regeneration strategies Hasseltia floribunda Kunth. (Flacourtiaceae), Inga densiflora Benth. (Fabaceae / Mimosoidae), Persea americana Mill. (Lauraceae), Tapirira mexicana Marchand. (Anacardiaceae) and Trichilia pittieri C. DC. (Meliaceae). A summary about the characteristics of the studied species is given in Table 1.

Table 1 Comparative information about study species, growth habit, geographical distribution, elevational range, regeneration strategy, dispersers, uses and additional information. References between brakets 

Ώ] (^{Croat, 1978}; ΐ] ^{Koptur, 1983}; Α] ^{Wheelwright, Haber, Murray, & Guindon, 1984}; Β] ^{Holdridge, Poveda, & Jiménez, 1997}; Γ] ^{Harvey & Haber, 1998}; Δ] ^{Wolstenholme & Whiley, 1999}; Ε] ^{Wehncke & Dalling, 2005}; Ζ] ^{González & Poveda, 2007}; Η] ^{González, 2010}; ⎖] ^{Zamora & Pennington, 2001}; ⎗] ^{Davidson, Mauffette, & Gagnon, 2002}; ⎘] ^{Arroyo-Rodríguez & Mandujano, 2006a}; ⎙] ^{Arroyo-Rodríguez & Mandujano, 2006b}; ⎚] ^{López-Gómez, Williams-Linera, & Manson, 2008}; ⎛] ^{Jiménez & Rodríguez, 2006}; ⎜] ^{Sugiyama & Peterson, 2013}).

Seedling collection: Seedlings from I. densiflora where obtained from seeds collected in December 2009. For the rest of the species, recently germinated seedlings were collected following the trails within a primary forest fragment at LCBS, between September and December 2009. Seeds and recently germinated seedlings were planted in plastic bags of 6 x 8 cm filled with soil taken from the field. All seedlings were grown in the greenhouse of LCBS. The greenhouse was covered with green shade cloth and seedlings were irrigated daily during the dry season and kept in the nursery until transplantation to the field. The maintenance in the nursery for seven months allowed the homogenization of initial conditions for all the individuals. Transplantation into the field was done in August 2010 during mid rainy season to avoid the risk of drying out and increase the probability of survival. We selected seedlings of similar size and excluded plants damaged by herbivores or disease.

Plot location: We worked in four sites having secondary forest fragments and adjacent pastures. The sites were separated by at least 1 km and shared a common history of land use. Secondary forest fragments had 15-25 years of regeneration and were at least 15 ha in size. As with most of the remaining forests in the area, the fragments were originally used for coffee production and cattle ranching and were located along rivers or steep terrain. Canopy height ranged 10-20 m, and forest cover ranged 75-86 %. The pastures were used for agriculture or cattle ranching for at least 15 years, but were recently abandoned. Soils are volcanic, moderately acidic with high inorganic matter and low phosphorus (^{Holl et al., 2011}). We do not have information about specific differences in soil conditions between plot sites; however, previous studies in the area have shown that abandoned pastures have a great variation in nutrient levels and soil compaction (^{Holl et al., 2011}). Pastures were dominated by exotic grasses, such as Axonopus scoparius (Flüggé) Kuhlm., Pennisetum purpureum Schumach. and Urochloa brizantha (Hochst. ex A. Rich.) R.D. Webster. Other common plants present in pastures included ruderal herbs, ferns, shrubs, small trees, and typical pioneer species such as Cecropia obtusifolia Bertol., Conostegia xalapensis (Bonpl.) D. Don ex DC., Croton draco Schltdl. & Cham., Heterocondylus vitalbae (DC.) R.M. King & H. Rob., and Pteridium arachnoideum (Kaulf.) Maxon.

In August 2010, we established 24 plots of 12 x 12 m. Three plots were established in each site (see above) within the secondary forest fragment while three plots were placed in random locations in adjacent pastures, maintaining at least 10 m of distance relative to the nearest forest edge. Plots within forest fragments were established in a stratified manner, avoiding large gaps while keeping a distance of at least 30 m from the edge. At three sites the pastures were abandoned and left for natural regeneration, but at the fourth site, cattle-ranching was still in place, and thus the study plots were fenced to exclude cattle. Five seedlings per species were planted within each plot both in secondary forest fragments and in pastures, keeping a distance of 2 m between seedlings, and distributed randomly. A total of 120 seedlings per species were planted, resulting in 30 seedlings per species per location, and 15 seedlings per species in each habitat type. Due to the lack of sufficient T. mexicana seedlings, this species was replicated in only three out of the four sites for both secondary forest frag- ments and pastures.

Seedling growth and survival: We carried out monthly measurements of height, diameter, number of leaves, herbivory damage, and seedling survival from August 2010 to August 2011. Seedling height was measured from the base of the stem to the tip of the highest meristem. Stem diameter was measured at the base of the stem right above the ground. Herbivory damage was recorded visually by estimating the percentage of leaf area loss for each leaf using a scale of 0 to 5 as follows: 0= absence of damage, 1= 1-20 %, 2= 21-40 %, 3= 41-60 %, 4= 61-80 % , 5= 81-100 %, where 100 % is whole leaf being lost. The percentage herbivory damage was average per plant. For the survival analysis, we considered dead seedlings as plants without leaves and with a dry stem at the time of measurement. Dead seed- lings were checked during successive visits to corroborate the lack of recovery.

Measurement of LMA: At the end of the experiment (August 2011), we collected one leaf from all surviving seedlings to deter- mine LMA following the methodology of (^{Garnier, Shipley, Roumet and Laurent, 2001}). In every individual, we selected the youngest full expanded leaf with at least 80 % of the leaf blade intact. Although we tried to collect leaves without herbivory or pathogen damages this was not possible for some seedlings growing in pastures. Leaf area was measured with a leaf area meter (Delta-T area meter-Devices) and all leaf samples were oven-dried at 60 °C until constant weight.

Measurement of canopy structure: We took hemispherical photographs in January 2011 to measure canopy openness and leaf area index (LAI) and assess how canopy structure affected seedling growth in the understory of secondary forests. Photographs were taken in the corners and at the center of each plot at a fixed height of 1.5 m above the ground, aligning the top of the camera lens with the magnetic North. Photographs were taken before 9 am, or after 3 pm, under overcast conditions to prevent direct flecks of light to blur the contrast between canopy cover and open sky (^{Rich, 1990}). Photographs were not taken in pastures due to the absence of a forest canopy there. Photographs were analyzed using Gap Light Analyzer (Forest Ecology Lab, Canada).

Statistical analysis: We used mixed-effect models (containing random and fixed effects) to analyze seedling growth (growth in height and diameter, and the number of leaves), as well as herbivory damage. We tested the effects of time (represented by the fixed-effect coefficient for time - 1), environment (which tested differences between secondary forests and pastures at the beginning of the experiment) and the interaction between time (time-1) and environment (secondary forest vs. pasture). We considered the effect of individual seedlings as random. Besides, we analyzed the data using site as a random effect and we compared models with Akaike information criterion, however the site had not effect, therefore we maintained and presented only the models without site as random effect. The models for variables height and diameter were corrected for the autocorrelation of errors within individual seedlings. We used the following fully crossed generalized linear model:

where n denotes the individual seedling, m corresponds to the month, e to the environment (secondary forests or pastures), Ynme is the measure of height, diameter, number of leaves or herbivory, θ is the overall mean of the corresponding variable (height, diameter, number of leaves, herbivory), α_m and β_e correspond to the “time” and “environment” fixed effects, respectively, γ_n is the “individual” random effect, (αβ)_me is the interaction term, and _εnme is the random error. For this analysis, we used the R packages nlme (^{Pinheiro, Bates, DebRoy, Sakar, & R Core Team, 2014}) and lattice (^{Sarkar, 2008}). To determine the effect of habitat type on seedling survival, we implemented a survival analysis using the product limit method (Kaplan-Meier) for census groups. For each species, we tested differences in survival curves between individuals growing in secondary forests and in pastures. To test differences among environments we used the Mantel-Haenszel test and the R package Survival (^{Therneau, 2014}).

We tested with a two-way factorial ANOVA the effect of species and environment (understory of secondary forests and pastures) in LMA. The LMA values were log-transformed to adjust the deviations of normality and equality of variances (^{Quinn & Keough, 2002}). A posteriori differences between groups (species and environment) were measured using a posteriori Tukey HSD tests. We measured differences in canopy structure between sites using a Kruskall Wallis test. All analyses were performed using R software (http://www.r-project.org).

Results

Variation in seedling stem height and diameter: Growth in height increased faster in pastures relative to secondary forests, especially in I. densiflora and P. americana, followed by T. mexicana. In contrast, H. floribunda and T. pittieri had small height differences between secondary forests and pastures (Table 2, Fig. 1).

Table 2 Parameters estimated by the mixed model to explain height, diameter, number of leaves and herbivory in seedlings of five tree species growing over 13 months in pastures and secondary forests. Statistical significance: *<0.05, **<0.005, ***<0.001 

Fig. 1 Monthly means of height and diameter in seedlings of five tree species growing in forest or pastures during 13 months. Lines represent predicted values according to mixed models. 

Within secondary forests, growth in height was low across species, with 4 out of 5 species showing annual average increments of less than 3.5 cm (except for T. mexicana, which had an average annual increase of 6 cm). All species significantly increased height in pastures, with average values increasing 30-300 % relative to the initial size (Fig. 1). Changes in diameter followed the same pattern across species and environments. Inga densiflora, T. mexicana and P. americana had a much greater increase in diameter in pastures (Table 2, Fig. 1).

Variation in leaf numbers: Seedlings of T. pittieri, I. densiflora and P. americana had significantly more leaves in pastures than in secondary forests; by contrast, seedlings of H. floribunda had more leaves in secondary forests (Table 2, Fig. 2).

Fig. 2 Monthly means of number of leaves and the index of herbivory for seedlings of five tree species growing in the understory of secondary forest and in pastures during 13 months. Lines represent predicted values according to mixed models. 

Hasseltia floribunda and P. americana decreased leaf numbers in secondary forests and pastures throughout the experiment, whereas T. mexicana decreased leaf numbers only in pastures (Table 2, Fig. 2). Inga densiflora was the only species increasing leaf numbers in pastures (Table 2, Fig. 2). Seedlings of H. floribunda, and T. mexicana decreased leaf numbers faster in pastures than in the secondary forests where leaf numbers did not change significantly over time in T. mexicana (Table 2, Fig. 2).

Variation in levels of herbivory: The index of herbivory was consistently higher in pastures for T. mexicana, T. pittieri, and H. floribunda, and in secondary forests for P. americana. Except for T. mexicana and P. americana, herbivory increased throughout the experiment. Herbivory increased faster in pastures for H. floribunda and T. pittieri, and was higher in secondary forests for I. densiflora and P. americana towards the end of the experiment (Table 2, Fig. 2). The tendency showed a sustained increased in herbivory, which peaked around the fourth and sixth month, and then decreased in all species.

Seedling survival: Survival trajectories of H. floribunda and I. densiflora were higher in secondary forests, whereas the rest of the species presented higher survival in pastures (Table 3, Fig. 3).

Table 3 Results of the Mantel-Henszel test comparing survival curves after 13 months in seedlings of five tree species growing in the understory of secondary forests ( SF) and in adjacent pastures (P), where N is the overall number of records (dead=0 or alive=1) and the observed (Obs.) is the number recorded as alive. 

The symbol * denotes statistically significant differences

Fig. 3 Survival probability curves of seedlings of five tree species growing in the understory of secondary forests and in adjacent pastures. 

Hasseltia floribunda and I. densiflora had high mortality in pastures (more than 50 % of individuals were lost in pastures), but in the secondary forests they lost only 6 and 5 seedlings, respectively, throughout the study period. Tapirira mexicana had an overall low mortality, whereas T. pittieri lost more than 50 % of the initial seedlings in both environments (Fig. 3, Table 3). Persea americana showed the highest mortality of all species in both environments, although survival was higher in pastures. The high survival of H. floribunda and I. densiflora in the secondary forests was associated with slow growth in the shade (Fig. 3, Table 3).

Variation in LMA: We found differences among species and environments in LMA (r² = 0.63, F_9,277 = 53.8, P<0.001). LMA was consistently higher in pastures relative to secondary forest (F_1,277 = 237.9, P<0.001, Fig. 4), however the difference in LMA between environments within species was significant among species (F_4,277 = 7.34, P<0.001); the difference in LMA between environments was large for some species as Inga densiflora but small for species as H. floribunda (Fig. 4).

Fig. 4 Leaf mass per area (LMA) of seedlings of 5 tree species in the understory of secondary forests and in pastures. Plants growing in pastures had higher LMA than plants growing in secondary forest across all species. Horizontal lines represent the median, boxes represent the 25^th and 75^th percentiles, whiskers represent 95 % confidence intervals according to the normal distribution, and points represent outliers. 

The LMA also varied between species (F_4,277 = 54.22, P<0.001), Tapirira mexicana had the highest LMA but not significantly different to T. pittieri and P. americana (Tukey HSD P>0.05), Inga densiflora and H. floribunda had lower LMA values and significant differences between them (Tukey HSD P<0.05) (Fig. 4).

Variation in forest structure and light conditions within secondary forests: Average canopy openness in the four secondary forest sites was 18.6 % with values ranging from 13.9 to 24.1 %. Canopy openness did not change significantly between sites (Kruskal- Wallis= 7.264, df = 3, P= 0.06). LAI values varied between 1.5 and 2.04, with an average of 1.77. Differences in canopy openness and LAI between sites did not affect seedling growth and survival within forest fragments.

Discussion

In this study, we found a variety of growth responses to different light conditions in two environments. Hasseltia floribunda and I. densiflora survived well in the secondary forest, whereas T. mexicana maintained a high survival rate in both secondary forests and pastures. Persea americana showed the highest mortality, but at the same time, it had high growth in pastures. Finally, T. pittieri showed low survival and growth in both environments. Due to its good survival and growth Tapirira mexicana has a great potential to restore pastures and secondary forests. The species had high growth under shade and intermediate growth in pastures, showing a flexible response to light availability. This species showed the highest values of LMA in both environments, which is an indicator of high photosynthetic rate (^{Kitajima, 1994}). Despite being a species typical of mature forests, T. mexicana is common in forest fragments and areas close to forest edges (^{Arroyo-Rodríguez & Mandujano, 2006a}; ^{Sugiyama & Peterson, 2013}). (^{Sugiyama & Peterson, 2013}) found high mortality in T. mexicana during the first year after germinating close to the forest edge, however after this period, seedlings were able to adapt to increased light levels. This could explain the variability observed in this species, with some individuals dying and some growing satisfactorily, since at the time of planting these seedlings had eight months in the nursery and were more mature.

Inga densiflora showed the highest growth in pastures and, being a nitrogen-fixing species, has great potential to restore degraded areas. (^{Davidson, Gagnon, Mauffette and Hernández, 1998}) reported for I. densiflora survival levels higher than 90 % in degraded pastures, higher than the levels observed here. The reason for this difference could be that the initial average height reported by (^{Davidson, Gagnon, Mauffette and Hernández, 1998}) was more than twice the initial average height in our study; this clearly favored growth and survival (^{Gerhardt, 1994}; ^{Martínez-Garza, Tobon, Campo, & Howe, 2013}). The initial diameter and seed- ling size has shown to influence survival and growth of tree seedlings planted in pastures (^{Mexal, Rangel, Negreros-Castillo, & Lezama, 2002}). Inga densiflora showed considerable plasticity, expressing the highest difference of LMA values between environments, with high values in the pastures and low values in the secondary forest, which also explains that this species showed the highest growth difference between environments. Inga densiflora is common in both primary forests and open areas and has a wide altitudinal gradient (^{Zamora & Pennington, 2001}). Thus, it may possess sufficient physiological plasticity to survive a wide range of environmental conditions. Although I. densiflora showed a high survival in the forest, it is possible that it requires the formation of big gaps to establish successfully.

While differences in growth and number of leaves were almost negligible among individuals in the secondary forest, herbivory increased all year, reaching the highest values at the end of the experiment.

Hasseltia floribunda and T. pittieri showed very slow growth in the understory of secondary forests and in pastures. These species are not suitable for restoration purposes in the studied environments, at least in the very early stages of succession. Hasseltia floribunda could survive under shade conditions, but the ability of this species to grow under low light is limited, this species had the lowest values of LMA and therefore, could have low capacity to increase biomass. In addition, H. floribunda is associated with wetlands and riparian forests, then, it could be affected by long drought periods (^{Harms, Condit, Hubbell, & Foster, 2001}). Finally, some individuals of P. americana grew at high rates in the pastures, but were associated with high mortality. Persea americana benefits from moderate light and requires a long time to store resources for growth and reproduction. It has high photosynthetic rates under high light, but is not a typical pioneer species (^{Wolstenholme & Whiley, 1999}). Since P. americana requires a variable period for resource storage, it is not a good choice for pasture restoration, being characteristic of later successional stages. Other strategies should be implemented in order to use these species successfully in restoration projects. In these species, increased growth responses could be improved if the seedlings are kept in nursery conditions until they are large enough to withstand stressful conditions.

Seedling performance varied within and among species for most of the variables measured. In general, growth and LMA were higher in the pastures, while survival, herbivory, and leaf number varied in direction and intensity that depend on the species and the environment. While the adverse abiotic conditions of pastures caused high seedling mortality, the increased light availability could benefit the species and individuals that could cope with the harsh conditions of pastures.

In general, our results are congruent with other studies that have assessed the behavior of native species planted in degraded pastures and secondary forests (^{Álvarez-Aquino et al., 2004}; ^{Muñiz-Castro, Williams-Linera, & Benítez-Malvido, 2015}).

Pastures have compacted and eroded soils, limited fertility and lower water soil content (^{Nepstad et al., 1996}; ^{Holl et al., 2000}). This was particularly evident in one site exposed to cattle ranching for nearly 50 years, where only 14 out of 75 seedlings survived. Low nutrient availability is associated with low seedling survival (^{Cole, Holl, & Zahawi, 2010}). Slow- growing species are particularly vulnerable to dry periods, since their roots usually do not reach sites with sufficient soil moisture. The increase in seedling mortality caused by exposure to the dry season and prolonged drought is well documented, both in natural conditions and in restoration projects (^{Gerhardt, 1994}; ^{Martinez-Garza et al., 2013}).

Growth in height and diameter were in general higher in pastures, and helped compensate for the higher herbivory observed in this environment. The high seedling mortality and high herbivory observed in pastures represents the outcome of the growth/mortality trade-off, which is characterized by growing fast under high light (^{Denslow, 1987}; ^{Guariguata, 2000}). These results are congruent with the stress tolerance model (^{Kitajima, 1994}), which proposes that seedling survival is related to a strategy of resource allocation that is mostly opportunistic, increasing growth to compensate for high mortality, or decreasing growth in return for lower mortality. Although diameter and height increased consistently in pastures this was not the case for leaf numbers (except in the case of I. densiflora, which maintained and even increased leaf number throughout the study). Low leaf production and increased leaf mortality in pastures could be the result of increased allocation to root biomass due to water stress and low nutrient availability (^{Gardiner & Hodges, 1998}; ^{Palow & Oberbauer, 2009}).

Forest structure could have affected the magnitude of LMA. All the species consistently had higher LMA in pastures relative to secondary forest. This result is congruent with previous results reporting higher LMA under high light (^{Lusk, Reich, Montgomery, Ackerly, & Cavender-Bares, 2008}). Shade plants were expected to have low photosynthetic rates, and thus lower construction and higher maintenance costs relative to leaves produced under high light, and thus, lower LMA (^{Valladares & Niinemets, 2008}). Also, the results are consistent with survival patterns; species with high LMA had higher survival in pastures while species with lower LMA had higher survival in secondary forest.

Many tropical areas are regenerating after long periods of deforestation, intense agriculture and cattle ranching. Natural regeneration combined with active reforestation is slowing down the global deforestation rate, although the net rate of forest loss continues to increase as old-growth forests are altered and then replaced by regenerating secondary forests (^{Wright, 2010}; ^{Aide et al., 2013}). Most of the regenerating forests and abandoned pastures are heavily degraded and are located within a fragmented landscape, which makes restoration difficult. The species composition of restored forests is affected by the landscape context (^{Dent & Wright, 2009}), the limited knowledge of the requirements to propagate individual species (^{Hoffmann, Blum, Velazco, Gill, & Borgo, 2015}), as well as by the specific goals of private owners and local farmers, who favor the regeneration of certain species, using selected species for logging, shade for cattle, fruiting trees, and medicinal purposes (i.e., ^{Häger, Otárola, Stuhlmacher, Castillo, & Arias, 2015}). The sun-shade dichotomy has practical importance but ignores the ample variation found in the regeneration strategies of tropical species; the species analyzed here are no exception. Many species express ontogenetic niche shifts as they increase in height and move from a light-limited environment to more light, or as they acquire resources to survive in the shade or increase growth under sun (^{Kitajima & Poorter, 2008}; ^{Benitez-Malvido & Martínez- Ramos, 2013}).

Although it is clear that successional forests and pastures will not reach the same level of species diversity and community structure relative to the original primary forests in the short run (^{Dent & Wright, 2009}; ^{Gibson et al., 2011}), they serve as reservoirs of biodiversity, and if managed properly, they could complement the environmental services provided by primary forests (^{Gardner et al., 2010}; ^{Melo, Arroyo-Rodríguez, Fahrig, Martínez-Ramos, & Tabarelli, 2013}). Conservation efforts should not abandon the protection of mature tropical forests, but at the same time, research should also focus on the ecological determinants of the long-term persistence of biodiversity in human- altered landscapes by integrating knowledge generated in temperate and tropical areas, hopefully leading to improved management and regenerating of secondary forests and pastures (^{Lindenmayer, 2010}). Increasing our knowledge on the regeneration requirements of tropical species is thus crucial to match seedling requirements with environmental conditions.

Reforestation and restoration projects have increased in the last decades. Nonetheless, our knowledge about the growth and survival of most tropical tree species in degraded habitats is scarce and has mostly limited to a small group of species, usually those with economic importance. Exploring the behavior of different species is relevant in order to achieve successful restoration projects (^{Palma & Laurance, 2015}). For instance, tropical montane forest is one of the most threatened ecosystem but very few works have addressed the potential of native species to restore this habitat.

In this study, we showed that Inga densiflora and T. mexicana have potential for restoring degraded pastures or forests. In contrast, H. floribunda, P. americana and T. pittieri showed negative results and other methods should be implemented to improve the establishment success of those species. The differences in growth responses observed within and among species were congruent with the life history strategies of our study species and their level of physiological plasticity to adapt to changing environmental conditions. For instance, Inga densiflora and T. mexicana grow naturally inside mature forests but can be found in open areas or forest edges as well.

Since many tropical areas are abandoned after agriculture and cattle ranching, the opportunity to implement successful restoration projects depends on how much we know on the specific physiological requirements of seedlings of native species and their functional growth responses (^{Wright, 2010}). Although the seedling stage is the most critical phase in the life cycle of plants, regeneration studies should include other life stages, such as juveniles and adults, since many tropical species express ontogenetic niche shifts and changes in long-term performance (^{Dalling et al., 2001}; ^{Benítez-Malvido, & Martínez-Ramos, 2013}). Our understanding of the importance of specific functional traits (such as LMA), as well as the variation in suites of functional traits, depends on the implementation of long-term demographic studies with sufficient replicates per ontogenetic stage, light conditions, and life forms (^{Clark & Clark, 1992}; ^{Poorter et al., 2008}; ^{Wright et al., 2010}), and hopefully, corrected by phylogenetic bias. The generation of this information has been long overdue, considering that human impacts on natural systems are becoming global and are accelerating the progression of climate change (^{Loarie et al., 2009}), which is likely to affect more intensively shade tolerant species, and in general, species exploiting limited resources and disturbed conditions.