Growth performance of sixty tree species in smallholder reforestation trials on Leyte, Philippines
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- Schneider, T., Ashton, M.S., Montagnini, F. et al. New Forests (2014) 45: 83. doi:10.1007/s11056-013-9393-5
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Although many reforestation projects have attempted to mitigate deforestation in the Philippines, most have focused on planting introduced trees, often with low success rates. A smallholder-based project in the Visayas region planted native species instead. This study assessed the growth performance of forty-four native and sixteen introduced species in 25 sites established by this project between 1995 and 2000. Diameter at breast height and total height were measured for 2,789 trees. Mean annual increments for diameter (MAID) at breast height and height (MAIH) were significantly higher for trees planted on limestone-influenced soils (MAID = 1.19 cm/year; MAIH = 1.05 m/year) than on purely volcanic soils (MAID = 0.81 cm/year; MAIH = 0.78 m/year). Growth of two native species, Melia dubia and Terminalia microcarpa, was higher than that of the widely planted exotic Swietenia macrophylla. The height increment for the highest-performing dipterocarp species, Shorea guiso, Shorea contorta, and Parashorea malaanonan, was not statistically different from the MAIH of S. macrophylla. A range of soil characteristics predicted performance, with organic matter predicting growth for six species, and percent nitrogen and percent clay predicting performance of five species. These findings show that certain native species can perform better than some exotic species when planted in open areas. They also disprove the widely held belief in the Philippines that Dipterocarpaceae cannot be planted in grasslands, and suggest that dipterocarps can be used successfully in reforestation. Finally, the findings show that more research is needed on species-site matching and on silvicultural management of native species plantations.
KeywordsDipterocarpaceaeGrowth ratesRestorationShorea spp.Swietenia macrophyllaVisayas
Large-scale logging of primary dipterocarp forest and subsequent conversion of cut-over forests to agricultural lands has led to the reduction of forest cover in the Philippines from 70 % of the land area in the early 1900s to under 17 % by the end of the twentieth century (Lasco and Pulhin 2006; Suarez and Sajise 2010). Commercial logging in the Philippines began at the start of the twentieth century. Following the trajectory of commercial forest exploitation found in other Southeast Asian countries, many logged areas in the Philippines were converted to farms and, once soil productivity declined, were turned into pasture or coconut plantations (Garrity et al. 1997; Lawrence 1997; Chokkalingam et al. 2006; Sales-Come and Hölscher 2010). Escaped fires or abandonment in many cases have led to colonization by Imperata cylindrica (L.) Raeusch., a fire-tolerant grass which impedes natural regeneration to secondary forest (Garrity et al. 1997; Göltenboth and Hutter 2004; Suarez and Sajise 2010). Garrity et al. (1997) estimate that 17 % of the Philippines is covered by Imperata. While the government classifies all land with slopes of 18 % or more as “forest land”, regardless of cover, only 41 % of these areas are actually under forest cover, leaving almost 60 % of designated forest land to be reforested (Chokkalingam et al. 2006).
Reforestation efforts in the Philippines have mostly focused on large-scale monoculture plantations of exotic species, such as Acacia mangium Willd., Gmelina arborea Roxb., and Swietenia macrophylla King (Freese 1983; Lasco and Pulhin 2006; Chokkalingam et al. 2006; Tolentino 2008). Between 1960 and 2002, about 1.7 million ha of land were planted, primarily with exotic tree species. Exotics were favored over natives because of their wide adaptability and tolerance to stress, because they were perceived to grow faster than native species, because germplasm was widely available, and because their silviculture was better understood (Tolentino 2008). However, the overall success of these reforestation efforts was low, with survival rates in some areas as low as 30 % (Margraf and Milan 1994; Lasco and Pulhin 2006).
In response to these large-scale efforts focused on exotic species, the Visayas State University (VSU) and the German bilateral aid organization GTZ (Gesellschaft für Technische Zusammenarbeit) developed the ‘rainforestation’ methodology in 1992, which promoted community-based reforestation primarily focused on native species (Margraf and Milan 1994; Milan and Göltenboth 2005). Since then, the rainforestation technique has been disseminated by VSU, and was declared one of the official reforestation methods of the Philippines Department of Environment and Natural Resources (DENR) in 2004 (Lasco and Pulhin 2006). The rainforestation methodology builds on the assumption that farming systems in the humid tropics are increasingly more sustainable as the system’s structure and function become more similar to those of local rainforests. The methodology aims to provide a staggered income from high-value timber as well as from fruit, spices, and medicinals. The rainforestation methodology also aims to increase biodiversity by augmenting the area planted with native tree species, and to help restore soil productivity and protect watersheds on degraded sites.
The methodology proposes interplanting shade intolerant pioneer tree species at high stocking rates (2 m × 2 m) with shade tolerant canopy species (mainly Dipterocarpaceae) as well as fruit trees in open areas. Community-run nurseries produced seedlings of over sixty pioneer, dipterocarp, and fruit tree species by gathering seeds and wildlings from remaining forest fragments (Margraf and Milan 1994).
Between 1995 and 2000, VSU and GTZ worked with smallholders to implement the rainforestation method on 28 sites on the island of Leyte and developed a list of recommended species for planting on limestone and volcanic soil types. There are some recent studies on ecophysiological aspects (leaf morphology, sap flow and humus composition) on rainforestation sites that include measures of diameter and height for a subset of species on four sites (Dierick and Hölscher 2009; Navarrete et al. 2010; Sales-Come and Hölscher 2010). However, there is no study evaluating overall growth performance of different species across all of the sites.
Native species reforestation is complicated because less silvicultural knowledge exists for native species than for established plantation species. Also, dipterocarp forests are notoriously difficult to restore. Many dipterocarp species are found only at low densities in natural forest, and have limited dispersal ranges through recalcitrant seeds in periodic mast fruiting events (Kettle 2010). Further, dipterocarp species in past studies have been found to have poor survival and grow more slowly than pioneers or exotic tree species in open grasslands (Otsamo et al. 1996, 1997; Tolentino 2008). In addition, the family used to be categorized as shade obligate. More recently, studies have shown significant variations in shade tolerance among the different genera in the Dipterocarpaceae (Suzuki and Jacalne 1986; Ashton and Berlyn 1992; Ashton 1995; Ashton et al. 1995; Weinland 1998). While more recent research in Singapore has shown that native species, including certain dipterocarps, can successfully be planted in open lands (Shono et al. 2007), other studies demonstrate the need for nurse trees (Ashton et al. 1997, 1998). Some research has also shown that dipterocarps performed well in enrichment plantings in semi-open selectively logged plantations (Millet et al. 2013). However, understanding of silvicultural requirements and growth rates of dipterocarps and other native tree species is still limited in the Philippines (Langenberger 2006; Tolentino 2008).
Further, knowledge about habitat ranges of many native species in the Philippines is lacking, and more work is needed to determine species-site interactions and site requirements for the long-term sustainability of reforestation efforts (Langenberger 2004, 2006; Santos Martín et al. 2010). Beyond soil type (volcanic or limestone), taking into account other individual site characteristics such as soil fertility parameters, soil texture, elevational range, position and aspect of slope, shade tolerance, and drainage class requirements could help improve survival and growth rates in reforestation projects (Ashton et al. 2001). Due to the conversion of nearly all of the lowland forest to agricultural uses in Leyte, current species distributions need to be combined with analyses of microhabitat and site conditions to predict the original ranges. Prolonged trials on species-site matching would be an important contribution to the success of reforestation projects (Wishnie et al. 2007; van Breugel et al. 2011), but in many cases this not feasible due to lack of funding. In most established reforestation sites, little information is available on survival rates and other indicators of success. Comparisons of species performance across a range of soil types in an active reforestation setting is therefore a feasible way to help fine-tune site preparation and species composition for future plantings (Langenberger 2006).
This study therefore aims to improve the silvicultural understanding of native species in the Visayas region by assessing growth and performance of the species planted in 25 smallholder rainforestation sites between 1995 and 2000. Species choice and site-species matching are key decisions in reforestation projects, and there is little published data available to compare performance in actual plantings. This is especially true for native species, for established trees, and for smallholder-managed sites. Since rainforestation is now promoted at the national level, and could inform restoration efforts in Imperata grasslands in other parts of Southeast Asia, data on performance of a wider range of native and exotic species are an important addition to the reforestation literature.
Materials and methods
Of the 28 sites established by the project, 25 were sampled (Fig. 1). Three sites were not included in this study due to access restrictions. Size of the sites ranged from 0.25 to 5.4 ha on both volcanic and calcareous soils. Planting design, stocking rate, and species composition varied widely across sites according to landowner preference and seedling availability at the time of establishment. A total of 60 tree species were identified (“Appendix”). Since sites were planted according to availability of planting stock in the VSU nursery, there was little overlap in species composition across sites. Planting locations were chosen by landowners in collaboration with VSU staff, and site preparation, planting and weed management were conducted by project staff for 11 of the 25 sites. The landowners chose to implement the planting in 14 cases, with support from VSU for seedling procurement and weed management. In all cases, seedlings and technical assistance were provided free of charge by VSU-GTZ project staff.
At all sites, total tree height and diameter at breast height (DBH) (1.4 m) of planted individuals were measured with a SUUNTO clinometer and diameter tape and trees were identified to species. Site characteristics (elevation; slope; aspect; previous land use) were recorded, and data on plot establishment and management (year of establishment; evidence of disease, fire, flooding, livestock, or other disturbance; post-harvest treatments, trees harvested) were compiled from baseline information collected by VSU and from interviews with landowners and project staff, and validated during site assessment. A pooled composite soil sample was taken from each site with a 20 cm soil auger and soil samples were analyzed by the VSU Department of Agronomy and Soil Science and the Philippine Rootcrops Research and Training Center.
The sampling methodology was adapted to the three types of rainforestation sites encountered: sites planted in straight lines, sites with scattered arrangement, and sites with high mortality with few surviving trees. On sites planted in lines, 2 m × 30 m parallel line transects were established based on randomly chosen lines, and all trees in each transect measured for a total of at least 100 live trees per site (nine sites). On sites planted with scattered distribution, randomly chosen 6 m × 10 m fixed plots were established along a NSEW grid and all trees measured within each plot for a total of at least 100 live trees per site (four sites). In sites with high mortality, all surviving trees were measured in a site census (twelve sites).
Mean annual increment for diameter (MAID) and height (MAIH) measurements were calculated for all species and all sites by dividing height and diameter values in 2011 by plantation age. One-way analyses of variance (ANOVA) were performed on the MAI values of individual trees to test the significance of soil types across all species, as well as to test species effects on MAID and MAIH for the twenty most frequently sampled species across all sites. A Tukey test was run on the MAI values of these twenty species to determine which mean growth increments were statistically different from each other. No interaction effect was tested due to the highly unbalanced data with high variability in species composition between sites. Regression analysis was used on soil variables for the MAID values of individual trees of the nine species found in at least five sites with at least five individuals each to identify significant predictors of species growth performance. Regression analysis was also performed for MAIH values, but since fewer soil variables were found to be significant, and the coefficient values were smaller, these results are not included here.
One-way ANOVA of mean annual increment for diameter and height across limestone and volcanic sites
Mean MAI DBH
Mean MAI height
Mean annual increment of diameter at breast height (MAID) and tree height (MAIH) of the 20 most frequently sampled species in twenty-five rainforestation sites in Leyte province, Visayas region (Philippines)
Melia dubia Cav.
Terminalia microcarpa Decne.
Swietenia macrophylla King
Furniture, woodwork, construction
Shorea guiso (Blanco) Blume
Artocarpus odoratissimus Blanco
Fruit tree, light construction
Agathis philippinensis Warb.
Dracontomelon dao (Blanco) Merr.
0.98 c, d,e
Toona philippinensis Elmer
Vitex parviflora A. Juss.
High quality furniture, posts and poles
Pterocarpus indicus Willd.
High quality furniture
Shorea contorta S. Vidal
Casuarina equisetifolia L.
Artocarpus heterophyllus Lam.
Furniture, light construction, tool handles
Dipterocarpus grandiflorus Blanco
Parashorea malaanonan (Blanco) Merr.
Hopea plagata (Blanco) S. Vidal
Hopea malibato Foxw.
Calophyllum blancoi Planch. & Triana
Podocarpus rumphii Blume
Intsia bijuga (Colebr.) Kuntze
In a Tukey comparison of means, the diameter growth rates of the two highest performing species (M. dubia and T. microcarpa) were found to be significantly different from those of the third-fastest growing species and most frequently found exotic tree, S. macrophylla. The diameter and height growth increments for the highest performing dipterocarp species, Shorea guiso, was found to be statistically similar to S. macrophylla. The height increment of two other dipterocarp species, Shorea contorta and Parashorea malaanonan was also found to be statistically similar to the MAIH of S. macrophylla.
Significant predictorsa of mean annual increment of diameter (MAID) at breast height in nine species found with more than five individuals at more than five sites
Regression coefficient for independent variable
CEC mE/100 g
Exch K mg
Exch Na mg
Exch Ca mg
Exch Mg mg
Extrac Mn mg
Exch Al mE/100 g
c = −0.018*
c = −0.020***
c = −0.020***
c = 0.013***
c = 0.00022***
Contrary to the widely held belief that native species, and especially dipterocarp trees, perform poorly when planted in the open and on degraded lands invaded by I. cylindrica (Suzuki and Jacalne 1986; Otsamo et al. 1996, 1997; Tolentino 2008), our results demonstrate that these species can be used successfully in restoration of grasslands. Also, although exotics have in many cases been favored in reforestation projects due to the assumption that they grow faster than native species, the findings presented in our study show that two native species M. dubia and T. microcarpa had statistically higher mean annual height and diameter increments than S. macrophylla in the 25 rainforestation sites assessed on Leyte. In addition, the dipterocarps S. guiso, S. contorta and P. malaanonan were all found to have statistically similar height growth to S. macrophylla in the sites visited, and S. guiso also showed statistically similar diameter growth to S. macrophylla.
These results support the assessments by Shono et al. (2007) and Santos Martín et al. (2010) that native trees, including some Dipterocarpaceae, can survive and perform well in open degraded sites. Native tree species therefore merit further research into silvicultural management and site-species matching to improve survival and performance (Langenberger 2006; Wishnie et al. 2007; Millet et al. 2013). In fact, M. dubia and Shorea sp. were chosen as priority trees for smallholder-oriented domestication projects in the Philippines in 2000 (Gunasena and Roshetko 2000). However, domestication efforts remained limited, probably due to problems with germplasm multiplication, distribution, and availability. Information about germplasm and nursery management, and silviculture of native species is still much less developed than for commonly planted exotics (Tolentino 2008). The growth rates provided by this study for forty-four native and sixteen exotic tree species help improve understanding of native and exotic species for future reforestation projects. For most of these species, no published data on growth performance exist, and most of the studies focus on recently established plantings. There are very few data points for plantations of more than 10 years, or for smallholder-managed sites. Thus, this study helps build knowledge about native species management, and provides a comparison point for relative species and site performance (“Appendix”).
However, this study does not take into consideration several important factors that influence tree performance, including site management and frequency and intensity of weeding around planted trees. Future studies should also take into account smallholder-specific challenges in tree planting, such as capacity to access and manage tree germplasm, sufficient knowledge about plantation management, and information about and access to markets (Roshetko et al. 2008). Smallholders make decisions on whether or not to plant native trees for different reasons than researchers or large-scale reforestation projects. They are less likely to plant trees if they do not have secure tenure for their land, and if they still have access to remaining natural forest areas (Santos Martín et al. 2012). Accordingly, interest in site care and maintenance varied widely among the smallholders interviewed, and several had passed away, fallen ill, or emigrated. Since planting design across sites was highly variable, and because it was not possible to collect interview information from all landholders, this study could not quantify site management throughout all sites assessed.
Our study does indicate that many species do better in certain soil types and site conditions, suggesting better and more refined planting guidelines are needed. Species trials including different pure and mixed plots under varying levels of silvicultural management intensity (established on sites selected for a range of soil characteristics, slopes, elevation and aspect) might help advance site treatment recommendations for well-performing native species. Similar block experiments have led to important advances in silvicultural understanding of native species in Central America in different species combinations (Wishnie et al. 2007; Piotto et al. 2010; van Breugel et al. 2011).
Further research is also needed on the availability of markets and economic competitiveness of native timber species in the Philippines. Financial analysis comparing the profitability of native and exotic plantation timber in Central America has shown that certain native species can compete economically with widely planted exotics, such as Tectona grandis (Griess and Knoke 2011). While such studies do not yet exist for the Philippines, it also needs to be pointed out that the logging ban declared in the Philippines by President Benigno Aquino in February 2011 complicates smallholders’ ability to harvest native trees planted on their own land.
Smallholders therefore need to consider a variety of factors beyond growth rates when deciding which tree species to plant (Santos Martín et al. 2012). Depending on the landowner objective and desired end use for the trees planted (home construction, lumber sale, fruit production, soil restoration, watershed rehabilitation, erosion control, or biodiversity protection), other factors such as bole straightness, timber quality and density, fruit yield, and mast and habitat value for wildlife should also be considered when deciding on species composition of future sites. It should be noted that the wood density in the species planted might vary from density values on record, since density is affected by growth conditions and site characteristics (FAO 2006; Weber and Sotelo Montes 2008). Further research into the wood properties of planted native species could help facilitate their marketability and acceptance among landowners.
Finally, the high levels of tree species diversity encountered in the smallholder rainforestation sites also underscores the potential biodiversity benefits that native species reforestation efforts can provide. The study shows that both exotic and native species can perform well in forest restoration, and that continued research into species-specific nursery techniques, species-site matching, and silvicultural management of lesser-known native species is needed for successful forest restoration.
This research was funded by the Tropical Resources Institute at the Yale School of Forestry & Environmental Studies, and the Yale Southeast Asian Studies Council. We thank the Visayas State University for facilitating this study, especially the staff of the Institute for Tropical Ecology for their support during the fieldwork period; the field assistant team Antonio A. Fernandez, Ronilio B. Calipayan and Pedro Cuero Jr.; and the landholders for their cooperation during our data collection efforts. Finally, thanks to Elaine Hooper and three anonymous reviewers for their helpful comments and suggestions.