Tree species with potential for reforestation in coastal zones of the humid tropics

Tree species with potential for reforestation in coastal zones of the humid tropics Georgina Vargas-Simón1*, Marivel Domínguez-Domínguez2, Valentín Pando-Fernández3 and Pablo Martínez-Zurimendi3,4 1 División Académica de Ciencias Biológicas, Universidad Juárez Autónoma de Tabasco, Km 0.5 Ctra. Villahermosa-Cárdenas, 86090 Villahermosa, Tabasco, Mexico. 2 Colegio de Postgraduados, Campus Tabasco, Instituto de Gestión Forestal Sostenible (IUFOR), Perif. Carlos A. Molina, km. 3.5, Carr. CárdenasHuimanguillo, AP 24, 86500 H. Cárdenas, Tabasco, Mexico. 3 Instituto de Gestión Forestal Sostenible (IUFOR), Universidad de Valladolid-INIA, Av. Madrid 44, 34004 Palencia, Spain. 4 Colegio de la Frontera Sur, Ctra. Villahermosa-Reforma km 15.5, Ranchería Guineo, II sección, 86280 Villahermosa, Tabasco, Mexico. Abstract Aim of study: The native species of warm humid climates Ceiba pentandra, Tabebuia rosea, Gliricidia sepium, Enterolobium cyclocarpum and Brosimum alicastrum are often included in Mexican reforestation programs. We evaluated the growth response in sandy soils of these species that could serve as pioneers in the restoration of coastal areas. Area of study: Alluvial plain in Frontera, Tabasco, Mexico. Material and methods: A total of 1080 plants were planted in 2014 and evaluated for 23 months in 30 plots under a randomized block design with six replications. The sample plots each occupied 36 m2 (each with 16 plants). Survival percentage, stem height (SH), basal diameter (BD) and basal area (BA) were quantified. Survival and growth variables were analyzed using logistic regression and ANOVA for repeated measures, respectively. Main results: At the end of the experiment (2016), high survival was demonstrated in G. sepium (88 %) and in C. pentandra (86 %), while B. alicastrum presented total mortality at six months. The highest values of SH and BD were presented in C. pentandra (2.9 m and 7.8 cm, respectively) and in G. sepium (2.6 m and 4.2 cm, respectively). Gliricidia sepium differed significantly from C. pentandra in terms of BA (5.9 vs. 23 m2 ha-1, respectively). Research highlights: The native species C. pentandra and G. sepium presented high survival and growth in the sandy soils; G. sepium showed strong adaptation to the environment and C. pentandra offered suitable coverage, characteristics that are necessary for the success of reforestation and restoration programs. Additional key words: basal area; Ceiba pentandra; Gliricidia sepium; stem height; survival Abbreviations used: BA (basal area); BAp (basal area of each plot); BD (basal diameter); EC (electrical conductivity); SH (stem height) Authors’ contributions: GVS, PMZ and MDD performed the experiments. All authors conceived and designed the experiments, analyzed the data, wrote the paper and critically reviewed the manuscript for intellectual content. Citation: Vargas-Simón, G; Domínguez-Domínguez, M; Pando-Fernández, V; Martínez-Zurimendi, P (2022). Tree species with potential for reforestation in coastal zones of the humid tropics. Forest Systems, Volume 31, Issue 1, e003. https://doi.org/10.5424/fs/202231118291 Received: 27 Apr 2021. Accepted: 16 Feb 2022. Copyright © 2022 CSIC. This is an open access article distributed under the terms of the Creative Commons Attribution 4.0 International (CC BY 4.0) License. Funding: The authors received no specific funding for this work. Competing interests: The authors declare no competing interests. Correspondence should be addressed to Georgina Vargas-Simón: geor[email protected] Forest Systems 31 (1), e003, 9 pages (2022) eISSN: 2171-9845 https://doi.org/10.5424/fs/2022311-18291 INIA-CSIC OPEN ACCESS RESEARCH ARTICLE Introduction Tropical humid forest plays an essential role worldwide as a reservoir of carbon, source of products of economic value and provider of ecosystem services and biodiversity; however, it is an ecosystem highly affected by deforestation (Sabogal et al., 2013). In Mexico, the area of these forests has diminished dramatically in recent years (de la Cruz et al., 2019), mainly due to the activities of commercial agriculture, livestock production and urban expansion (Kolb & Galicia, 2018). The establishment of plantations for restoration has been proposed as a tool for rehabilitation of the forests, with the tree canopy shown to influence the recruitment of new species and the trees themselves potentially acting as carbon dioxide sinks (Pedraza & Williams, 2003). Implementation of reforestation programs with native species in degraded zones favors an increase in both wildlife habitat and biodiversity (Giannini et al., 2017). Coastal zones rank among those that require the most attention, since climatic change has triggered severe problems in these areas, in terms of erosion and flooding with a consequent loss of land and biodiversity (Ramos et al., 2016). These areas are characterized by the presence of 2Georgina Vargas-Simón, Marivel Domínguez-Domínguez, Valentín Pando-Fernández and Pablo Martínez-Zurimendi Forest Systems April 2022 • Volume 31 • Issue 1 • e003 sandy soils, with little water retention and intermediate fertility, pH values of between 6.3 and 6.7 and moderate salinity at certain times of the year (Palma et al., 2007). The introduced species that thrive best in these zones include Cocos nucifera L., Terminalia catappa (Gaertn.) Eichler and Casuarina equisetifolia L. (Moreno & Paradowska, 2009). On the other hand, of a total of 55 native species, those best suited to this habitat include Cedrela odorata L., Diphysa robinioides Benth., Enterolobium cyclocarpum (Jacq.) Griseb., Bursera simaruba (L.) Sarg., Gliricidia sepium (Jacq.) Kunth ex Walp., Tabebuia rosea Bertol. DC. and Chrysobalanus icaco L. (Moreno & Paradowska, 2009). This study evaluated the growth response of five native species of the warm humid climate that could serve as pioneers in the reforestation of coastal areas: Ceiba pentandra (L.) Gaertn.), T. rosea, G. sepium, E. cyclocarpum and Brosimum alicastrum Sw. Some of these species have been selected previously for reforestation programs in tropical zones of Latin America and Africa (van Breugel et al., 2011; Abengmeneng et al., 2015). However, there have been few studies addressing their growth in sandy soils or their response to high temperatures and unstable rainfall regimes as a probable future scenario brought about by climatic change. Material and methods Study species Species were selected considering their suitability and the availability of seedlings in the nurseries of the National Forestry Commission (CONAFOR, by its Spanish acronym), Gerencia Villahermosa (an official body responsible for plant propagation and distribution for reforestation) and Vicoplan (Viveros y Comercializadora de Plantas Jobel S.C. de R.L. de C.V). Gliricidia sepium is a multipurpose legume, generally used for live fences, fodder and pest control, and is an excellent contributor of organic material through its interaction with symbiont organisms (mycorrhizal fungi and nitrogen-fixing bacteria) (Canul et al., 2018; Villanueva et al., 2019; Ramos et al., 2020). C. pentandra is a fast-growing and highly valued tree; even in different regions of Africa where its wood is used to make canoes and domestic utensils (Abengmeneng et al., 2015). In Latin America, B. alicastrum has extra value as a food-producing tree for humans and livestock. E. cyclocarpum is used to provide shade for livestock and its seeds are used in handcrafts (Román et al., 2007; Bonilla & Holl, 2010), while T. rosea is used for timber and as a shade tree in pastures (Pineda et al., 2016). The natural habitats of these tree species are in dry and humid tropical forests of different successional status (Pennington & Sarukhán, 2005; Román et al., 2007). Study site The study area is located in Felipe Carrillo Puerto, in Centla, Tabasco, Mexico (18°53’1.54” N, 92°72’32.55” W: 2 masl). The climate is warm humid with abundant rains in summer (INEGI, 2019). During the 23 month period of evaluation, the average minimum and maximum temperatures were 20.0 ± 2.7 °C and 29.7 ± 3.5 °C, respectively. Rainfall was recorded at 1284.4 mm in 2014 (March-December), 2217 mm in 2015 (January-December) and 262.5 mm in 2016 (January-February) (Fig. 1). The soils are sandy in texture and classified as Arenosols (Palma-López et al., 2007). Soil pH was 6.9 and electrical conductivity (EC) was 0.608 dS m-1 (mean values from three compound samples taken at random in each block at a depth of 15 cm). Analysis was conducted with a Multi-Probe System YSI 556 MPS, 0 100 200 300 400 500 600 0 5 10 15 20 25 30 35 40 MAMJ J ASOND J FMAMJ J ASOND J F Precipitation (mm) Temperature (°C) Months T max T min pp Figure 1. Temperature and rainfall conditions recorded during the growth evaluation period of the study (March 2014-February 2016) in Felipe Carrillo Puerto, Centla, Tabasco, Mexico. Source: National Water Commission (CONAGUA, 2016). Forest Systems April 2022 • Volume 31 • Issue 1 • e003 3 Tree species for reforestation in a tropical coastal area using the methodology established in NOM-021-RECNAT-2000 (2000). The reference vegetation close to the experimental plots was a secondary forest, represented by trees such as B. simaruba, Guazuma ulmifolia Lam., C. odorata, T. rosea, G. sepium, Swartzia cubensis (Britton & P. Wilson) Standl. and Piscidia piscipula (L.) Sarg, among others (Manuel Núñez Piedra, CONAFOR, pers. com.). The area was cleared of weeds using a tractor, and seedlings of each species were planted in a 1.5 m × 1.5 m grid within 5 quadrangular plots of 9 m × 9 m (81 m2). A total of 1080 seedlings of five species were planted in 30 plots; 36 plants of the same species were established per plot (of which, to avoid edge effects, only the 16 plants in the center of each plot were measured) with a total of 96 sample plants per species. Five plots for each species were placed in a randomized complete block design, with six replications. The seedlings were six months old at planting and healthy in appearance, set in a root ball. The average values of stem height (SH) and basal diameter (BD) of the plants at the moment of planting were: 0.43 m and 0.84 cm (T. rosea), 0.27 m and 0.60 cm (E. cyclocarpum), 0.64 m and 1.2 cm (G. sepium), 0.54 m and 1.2 cm (C. pentandra) and 0.45 m and 0.5 cm (B. alicastrum). Manual irrigation was carried out (supplying approximately 4 L per plant, twice a week), but only during the spring of 2014, which was the dry period of the plantation year. Manual weeding was conducted every four months throughout the whole study period. G. sepium presented a shrub-like growth that produced various stems, and was pruned to leave only the most vigorous of these in order to subsequently measure a single stem only. In B. alicastrum, total mortality was recorded at six months of study, and this species is therefore excluded from the results. Survival was recorded and growth was evaluated by measuring SH and BD. These measurements were taken at the time of initial plantation and then at threemonth intervals until month 18, with a final measurement taken at 23 months after planting. The basal area of each plot (BAp, m2) was calculated (Eq. 1) and this value was further extrapolated to hectare level as basal area (BA, m2 ha-1) (Eq. 2). The BD (cm) of all plants in each plot was used for this purpose (Serrada-Hierro, 2008) as follows: 𝐵𝐵𝐵𝐵𝐵𝐵 = ( 𝜋𝜋 40000) · (∑𝐵𝐵𝐵𝐵𝑖𝑖2 ) (1) 𝐵𝐵𝐵𝐵 =𝐵𝐵𝐵𝐵𝐵𝐵 · 10,000 𝑆𝑆𝐵𝐵 (2) where: ∑ BDi2 is the sum of the squared value of the stem BD of all of the individuals quantified in the plot; and Sp is the surface area of the plot in m2. Statistical analysis In order to confirm compliance with the assumptions of normality, the Kolmogorov-Smirnov test was applied to the data. Since this assumption was not fulfilled, the data were transformed to a natural logarithm in order to carry out the statistical analysis. A two-way ANOVA was conducted for the vegetative growth of the four surviving species in order to determine differences among species. Survival was analyzed using a logistic regression for each of the seven measurement dates in Proc Logistics. The effect of two factors (block and species) on the probability of survival on each of the measurement dates (3-23 months) was evaluated using the following mathematical formula: 𝑝𝑝𝑖𝑖𝑖𝑖𝑖𝑖 =1 1 + exp⁡(−𝑍𝑍𝑖𝑖𝑖𝑖𝑖𝑖) in which 𝑍𝑍𝑖𝑖𝑖𝑖𝑖𝑖 =𝑙𝑙𝑙𝑙𝑙𝑙(𝑝𝑝𝑖𝑖𝑖𝑖𝑖𝑖 1−𝑝𝑝𝑖𝑖𝑖𝑖𝑖𝑖)=𝜇𝜇+𝛼𝛼𝑖𝑖+𝛽𝛽𝑖𝑖 where μ is the general population mean, αi is the effect of the i-th block and βj is the effect of the j-th species. These parameters were estimated using the method of maximum likelihood. SH, BD and BA were analyzed with a repeated measures (over time) model, using a linear mixed model with two inter-subject factors (species and block) in a random block design and one intra-subject factor (measurement date), with eight levels. A structure of first-order auto-regressive and heterogeneous variances (ARH1) was used for each species, with a total of 36 parameters of variance estimated using the method of restricted maximum likelihood (REML). This variance structure was selected because it gave the best values for the Bayesian Information Criterion (BIC). In addition, comparisons were made with the least square means estimated by the model, using the Tukey-Kramer test with a significance level of 0.05. Individual contrasts were applied to compare total growth during the experiment and comparisons were also made among particular species at a given sampling date. Normality of the studentized residuals was analyzed using the Kolmogorov-Smirnov test. All tests and statistical analyses were performed using the software SAS 9.4 (SAS Inst. Inc., Cary, NC, USA, 2017). Results The highest probabilities of survival at the end of the study (23 months) were found in G. sepium (0.88) and C. pentandra (0.86) (Fig. 2a). T. rosea (0.54) and E. cyclocarpum (0.52) presented lower survival probabilities 4Georgina Vargas-Simón, Marivel Domínguez-Domínguez, Valentín Pando-Fernández and Pablo Martínez-Zurimendi Forest Systems April 2022 • Volume 31 • Issue 1 • e003 (Fig. 2a). At the end of the experiment, the difference between the species with the highest and lowest survival probabilities was 36%. According to the statistical analysis of the (natural logarithm) transformed data we found highly significant differences among the species in three variables for the period studied (23 months): SH (F3,375 = 285.3, p<0.01), BD (F3,375 = 211.3, p<0.01) and BA (F3,15 = 37.62, p<0.05). The interaction species × measurement date (plantation age) was found to be significant for SH (F21,2024 = 34.1, p<0.01) and for BA (F21,2016 = 16.3, p<0.01). The Least Squares Means and the confidence intervals were converted by reversing the data transformation, as shown in Fig. 2b for SH and Fig. 2c for BA. Discussion Species survival Survival of C. pentandra and G. sepium was “excellent”, according to the classification of Elliot et al. (2003). These species have previously presented high survival rates, as demonstrated in the study of de Souza et al. (2010), who recorded 97.2% survival in C. pentandra, which had grown for six years in full sunlight in the Brazilian Amazon. In the case of G. sepium, González et al. (2017) reported survival that exceeded 86% at two months after transplanting in the Chamela-Cuixmala Biosphere Reserve (Jalisco, Mexico), which is characterized by its tropical dry forest and Regosol soil. It should be noted that G. sepium is commonly planted as live fencing and remains in the site for around 15 years, according to observations carried out in Tacotalpa, Tabasco, Mexico, where there a warm-humid climate prevails (Villanueva et al., 2015). Both of these species are considered pioneers in the successional process and present ecophysiological characteristics that give them greater tolerance to water stress and high solar radiation (Mayoral et al., 2017; Guimarães et al., 2018; Valverde & Arias, 2020). The association of G. sepium with nitrogen-fixing bacteria gives the species a greater opportunity for establishment (Canul et al., 2018). Survival of the species T. rosea and E. cyclocarpum was “acceptable” and that of B. alicastrum was “unacceptable”, according to the categories established by Elliot et al. (2003). However, when B. alicastrum was established in pastures in coastal dune soils in Veracruz (Mexico), its survival was reported as 48.5% (Laborde & Corrales, 2012). This tree species is late successional and is therefore unsuited to low soil moisture conditions (Laborde & Corrales, 2012). Species growth The soil conditions of low fertility and sandy texture, low availability of water due to the free draining character of the soil texture and low precipitation and high temperatures during the study period were favorable for growth of C. pentandra and G. sepium, but limiting for the other two species. A prolonged drought was recorded during Figure 2. Probability of survival (a), stem height (b) and basal area (c) of four tree species planted in Felipe Carrillo Puerto, Centla, Tabasco, Mexico. The error bars represent the standard error of the means Forest Systems April 2022 • Volume 31 • Issue 1 • e003 5 Tree species for reforestation in a tropical coastal area the period of study in 2014 and 2015, and these two years were consecutively catalogued as the warmest since 1971 (CONAGUA, 2014, 2015, 2016). The SH of C. pentandra recorded at 23 months after planting agrees with previous data recorded for trees of the same species 18 months after planting in pastures in the Lacandon area of Chiapas, Mexico (Román et al., 2012). In addition, fertilized plants were reported to reach heights of up to 10 m in 55 months in the Brazilian Amazon, in a soil classified as a Latosol (de Souza et al., 2010). With regard to G. sepium, de Oliveira et al. (2016) reported plant heights of 3.0-4.3 m in plantations from cuttings established in a Ferric Lixisol soil in Caatinga region, Brazil, which thus exceeded the values obtained in this study. In terms of stem BD, growth values ≥ 4 cm, as shown for C. pentandra and G. sepium in our study, are considered “acceptable” by Román et al. (2012) for tropical trees. These results are similar to those recorded by Joslin et al. (2016), in which C. pentandra presented an average BD of 4 cm one year after being planted in a loam soil with no fertilization in the Brazilian Amazon. Silva et al. (2012) found that G. sepium reached BD values of 4.8 cm when planted at a density of 800 trees ha-1 one year after being planted in the Mossoro region (Brazil), a dry tropical zone. In this experiment, C. pentandra presented the highest growth in BA, which agrees with the highest records of BD and survival obtained for this species in Atlantic Coastline plantations of Honduras 26 months after being planted in sandy soils (PROECEN, 2003). However, lower values (13 m2 ha-1) have also recorded in a succession experiment conducted within a protected natural area (Laguna Cartagena, Puerto Rico) characterized by low-deep stony soils with good drainage (Weaver & Schwagerl, 2008). Propagation of G. sepium is generally carried out using cuttings, so studies of BA in plants obtained from seeds are scarce. In this study, the species showed a BA value higher than the average value of 4.4 ± 1.5 m2 reported by Park et al. (2010), who evaluated G. sepium 2 years after its plantation in silty and clay soils under tropical conditions at Río Hato, Panama. This species was associated with another four species (Acacia mangium Willd., Ochroma pyramidale (Cav. ex Lam.) Urb., Erythrina fusca Lour. and Pachira quinate W.S. Alverson). Silva et al. (2012), in an experiment carried out in a zone typified by dry weather in Mossoro, Brazil, stated that G. sepium plantation densities of 400 and 1200 plants ha-1 produce minor differences in terms of plant height. These authors did record an inversely proportional relationship between plantation density and the crown diameter of individual trees. In this study, T. rosea and E. cyclocarpum recorded low height growth values of 1.2 m and 1.6 m, respectively. However, these values are similar to those of a study conducted in Mérida, Venezuela, of T. rosea under fertilized sandy loam soil conditions in which, 18 months after planting, the trees measured 1.2 m in height on average (Araque et al., 2009). Likewise, individuals of E. cyclocarpum reached a SH of 1.2 m in four years when planted in soils previously used for pasture in the central area of Veracruz, Mexico (Laborde & Corrales, 2012). On the other hand, E. cyclocarpum trees sown in Otoch Ma’ax Yetel Kooh, a natural reserve located between Campeche and Quintana Roo, Mexico, in which soils are known as rendzinas and lithosols, presented a SH of 50 cm after 24 months, which are low rates according to this analysis. In contrast, this legume can reach SH values of 5.5 m after two years in an African savanna environment (Arigbede et al., 2012). In T. rosea, the recorded value of stem BD in this study was 2.9 cm (Table 1), which is similar to those found by Plath et al. (2011) in Colon, Panama, in fertile soils. The average growth in BD was 2.9 cm two years after being transplanted and even greater, at 3.1-5 cm (Araque et al., 2009), in the studied conditions previously mentioned. The leguminous E. cyclocarpum had a low stem BD (3.1 cm); however, under the conditions of the African humid tropics, the BD reached 7.2 cm in 24 months (Arigbede et al., 2012). In the same context, T. rosea presented a BA of 2.9 m2 ha-1, similar to that found in silvopastoral systems from natural regeneration evaluated in Jinotega, Nicaragua (de Sousa et al., 2016), in which the wooded region had a BA = 2.5 m2 ha-1 and 14 m in height, and also similar to that reported in a mixed plantation including four more species (2.5 m2 ha-1) in Sardinilla, Panama (Salisbury & Potvin, 2015). Under natural conditions, E. cyclocarpum Species Stem height (cm) Stem basal diameter (cm) Basal area (m2·ha-1) Ceiba pentandra 289.7 ± 36.52 7.8 ± 1.33 23.0 ± 7.7 Gliricidia sepium 258.5 ± 23.00 4.21 ± 0.35 5.9 ± 1.0 Enterolobium cyclocarpum 164.7 ± 13.86 3.1± 0.23 2.1 ± 0.5 Tabebuia rosea 120.7 ± 5.12 2.9 ± 0.14 1.7 ± 0.2 Table 1. Growth variables measured (means ± standard error) in four tropical tree species at 23 months after planting. 6Georgina Vargas-Simón, Marivel Domínguez-Domínguez, Valentín Pando-Fernández and Pablo Martínez-Zurimendi Forest Systems April 2022 • Volume 31 • Issue 1 • e003 may present a higher (12 m2 ha-1) (Bonilla, 2019) or lower (1.4 m2 ha-1) BA (Park et al., 2010). The tree species included in this study are considered to be of fast growth (Araque et al., 2009; Plath et al., 2011; Silva et al., 2012). However, as stated by van Breugel et al. (2011), the same species can present different responses depending on soil texture, fertility and moisture content and the particular management practices employed. Other influential elements include the incidence of herbivory and the successional status of species, which are related to their capacity to compete with other plants (Plath et al., 2011). Bonilla & Holl (2010) attributed one low growth to light interference and competition with other plants. They deduced that, considering their pioneer characteristics, growth of these species would be higher in open areas with no vegetation. Although T. rosea did not present a good performance in the study area, its foliage has certain anatomical traits that might help it to tolerate high radiation through the presence of indument, a thick and ridged cuticle that acts to reflect excess light and vascular veins in the mesophyll that protect the tissue from excess radiation and facilitate water conservation (Araque et al., 2009). However, stomatal conductance can be inhibited at high temperatures (>32 °C) and photosynthetic rate can diminish (Araque et al., 2009) as was the case in the present study. Studies of the origin of E. cyclocarpum populations in Oaxaca, Mexico, therefore displayed differences in the recorded annual increase of height, BD and survival, according to the rainfall characteristics, as well as chemical and physical soil properties of each survey area (Hernández et al., 2019). The results obtained in this experiment increase the possibilities of using native species in reforestation and restoration programs in the dry tropics. Ceiba pentandra and G. sepium both meet the criteria for effective reforestation and are tree species with a high survival ratio, capable of crown expansion and high primary production in the sites where they have been planted (Douterlungne et al., 2015). G. sepium would be useful for increasing soil fertility in degraded ecosystems and providing fodder and fuel, as well as efficient carbon capture, in addition to its common use in agroforestry systems to provide shade for coffee and cocoa (Wishnie et al., 2007; Villanueva et al., 2015; Pantera et al., 2021). Moreover, rapid growth in SH, BD and BA would fulfill the objective of quickly reaching complete tree cover, and thus effect a possible acceleration of the ecosystem recovery process (Freitas et al., 2019). Reintroduction of native species can significantly increase levels of organic material in a system and serves to accelerate secondary succession in degraded and abandoned agricultural and livestock production areas (Román et al., 2007). It should be noted that, in an active restoration program, establishment of plants via the plantation method may be more expensive than direct sowing or passive restoration, given the costs implied in the maintenance of seedlings in nurseries and transplanting them to the field site (Freitas et al., 2019). However, ecological restoration is urgently required in order to counteract the high deforestation rate and this method may be very effective in terms of increasing floral and faunal diversity, as well as litter and biomass (Crouzeilles et al., 2017). The present study was conducted in a coastal soil in which the pH and EC did not present an impediment to the survival and growth of plants; the soil pH was almost neutral and EC was lower (0.608 dS m-1) than in saline soils (4 dS m-1). In order to enhance the potential of these promising species, a suitable fertilization program considering soil type is required (de Souza et al., 2010; Hall et al., 2011), as well as appropriate spacing among trees in order to facilitate improved growth and development. In summary, C. pentandra and G. sepium presented high survival and growth rate in stem height and basal area after 23 months from planting. These species maintained high plantation density and could thus be considered as useful species for reforestation and restoration programs in coastal zones given their favorable adaptation to the environment. E. cyclocarpum and T. rosea presented low survival values (technically), while B. alicastrum did not survive after six months from the time of plantation, demonstrating that the environmental conditions in open coastal soils did not favor this species. Acknowledgements Thanks to Álvaro Bellizzia Álvarez (deceased) for giving access to his land for the study, to Manuel L. Núñez Piedra and Jackelin Ruiz Vidal of the Mexican National Forestry Commission and to Vicoplan (Viveros y Comercializadora de Plantas Jobel S.C. de R.L. de C.V.) for their management and donation of plants. Thanks also to Jesús M. Ascencio Rivera and to the participating students of the Biological Sciences Academic Faculty from the University of Tabasco (División Académica de Ciencias Biológicas-Universidad Juárez Autónoma de Tabasco) for their considerable logistical support. References Abengmeneng CS, Ofori DA, Kumapley P, Akromah R, Jamnadass R, 2015. Estimation of heritability and genetic gain in height growth in Ceiba pentandra. Afr J Biotechnol 14: 1880-1885. Araque O, Jaimez RE, Azócar C, Espinoza W, Tezara W, 2009. Relaciones entre anatomía foliar, intercambio de gases y crecimiento en juveniles de cuatro especies forestales. Interciencia 34: 725-729. 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Selecting framework tree species for restoring seasonally dry tropical forests in northern Thailand based on field performance. Forest Ecol Manag 184: 177-191. https://doi.org/10.1016/ S0378-1127(03)00211-1 Freitas MG, Rodrigues SB, Campos-Filho EM, do Carmo GHP, da Veiga JM, Junqueira RGP, Vieira DLM, 2019. Evaluating the success of direct seeding for tropical forest restoration over ten years. Forest Ecol Manag 438: 224-232. https://doi.org/10.1016/j.foreco.2019.02.024 Giannini TC, Giulietti AM, Harley RM, Viana PL, Jaffe R, Alves R, et al., 2017. Selecting plant species for practical restoration of degraded lands using a multiple‐trait approach. Austral Ecol 42: 510-521. https:// doi.org/10.1111/aec.12470 González‐Tokman DM, Barradas VL, Boege K, Domínguez CA, del‐Val E, Saucedo E, Martínez‐Garza C, 2017. Performance of 11 tree species under different management treatments in restoration plantings in a tropical dry forest. Restor Ecol 26: 642-649. https:// doi.org/10.1111/rec.12617 Guimarães ZTM, dos Santos VAHF, Nogueira WLP, Martins NO de A, Ferreira MJ, 2018. Leaf traits explaining the growth of tree species planted in a Central Amazonian disturbed area. Forest Ecol Manag 430: 618-628. https://doi.org/10.1016/j.foreco.2018.08.048 Hall JS, Love EB, Garen JE, Slusser JL, Saltonstall K, Mathias S, et al., 2011. Tree plantations on farms: Evaluating growth and potential for success. Forest Ecol Manag 261: 1675-1683. https://doi.org/10.1016/j.foreco.2010.09.042 Hernández-Hernández ML, Velasco-García MV, López-Upton J, Galán-Larrea R, Ramírez-Herrera C, Viveros-Viveros H, 2019. Crecimiento y supervivencia de procedencias de Enterolobium cyclocarpum en la costa de Oaxaca, México. Bosque (Valdivia) 40: 173-183. https://doi.org/10.4067/ S0717-92002019000200173 INEGI, 2019. Prontuario de información geográfica municipal de los Estados Unidos Mexicanos. Centla, Tabasco. Instituto Nacional de Estadística y Geografía. https://www.inegi.org.mx/contenidos/app/mexicocifras/datos_geograficos/27/27003.pdf. [3 July 2020]. Joslin A, Markewitz D, Morris LA, de Assis OF, Kato O, 2016. Improved fallow: growth and nitrogen accumulation of five native tree species in Brazil. Nutr Cycling Agroecosyst 106: 1-15. https://doi.org/10.1007/ s10705-016-9783-0 Kolb M, Galicia L, 2018. Scenarios and story lines: drivers of land use change in southern Mexico. Environ Dev Sustain 20: 681-702. https://doi.org/10.1007/ s10668-016-9905-5 Laborde J, Corrales-Ferrayola I, 2012. Siembra directa de Brosimum alicastrum Sw. (Moraceae) y Enterolobium 8Georgina Vargas-Simón, Marivel Domínguez-Domínguez, Valentín Pando-Fernández and Pablo Martínez-Zurimendi Forest Systems April 2022 • Volume 31 • Issue 1 • e003 cyclocarpum (Jacq.) Griseb. (Mimosaceae) en diferentes habitats en el trópico seco del centro de Veracruz. 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Pantera Α, Mosquera-Losada MR, Herzog F, den Herder M, 2021. Agroforestry and the environment. Agrofor Syst 95: 767-774. https://doi.org/10.1007/s10457021-00640-8 Park A, van Breugel M, Ashton MS, Wishnie M, Mariscal E, Deago J, et al., 2010. Local and regional environmental variation influences the growth of tropical trees in selection trials in the Republic of Panama. Forest Ecol Manag 260: 12-21. https://doi.org/10.1016/j.foreco.2010.03.021 Pedraza RA, Williams-Linera G, 2003. Evaluation of native tree species for the rehabilitation of deforested areas in a Mexican cloud forest. New Forest 26: 83-99. https://doi.org/10.1023/A:1024423511760 Pennington TD, Sarukhán J, 2005. Árboles tropicales de México. Manual para la identificación de las principales especies. Univ. Nal. Autónoma de México, Fondo de Cultura Económica, Cd. de México, Mexico. Plath M, Mody K, Potvin C, Dorn S, 2011. Establishment of native tropical timber trees in monoculture and mixed-species plantations: small-scale effects on tree performance and insect herbivory. Forest Ecol Manag 261: 741-750. https://doi.org/10.1016/j.foreco.2010.12.004 Pineda-Herrera E, Valdez-Hernández JI, Pérez-Olvera CP, 2016. Crecimiento en diámetro y fenología de Tabebuia rosea (Bertol.) DC. en Costa Grande, Guerrero, México. Acta Univ 26: 19-28. https://doi. org/10.15174/au.2016.914 PROECEN, 2003. Estudio de comportamiento de especies maderables nativas con importancia comercial del bosque húmedo. Guías silviculturales de 23 especies forestales del bosque húmedo de Honduras. Escuela Nacional de Ciencias Forestales (ESNACIFOR), Organización Internacional de las Maderas Tropicales (OIMT). Ramos-Reyes R, Gama-Campillo LM, Núñez-Gómez JC, Sánchez-Hernández R, Hernández-Trejo H, Ruiz-Álvarez O, 2016. Adaptación del modelo de vulnerabilidad costera en el litoral tabasqueño ante el cambio climático. Rev Mex Cienc Agric 13: 2551-2563. https:// doi.org/10.29312/remexca.v0i13.478 Ramos-Trejo OS, Canul-Solís JR, Alvarado-Canché ADR, Castillo-Sánchez LE, Sandoval-Gío JJ, Campos-Navarrete MJ, et al., 2020. Growth, forage yield and quality of Morus alba L. and Gliricidia sepium (Jacq.) Walp. in mixed and pure fodder bank systems in Yucatan, México. Agroforest Syst 94: 151-157. https://doi.org/10.1007/s10457-019-00378-4 Román-Dañobeytia F, Levy-Tacher S, Perales-Rivera H, Ramírez-Marcial N, Douterlungne D, López-Mendoza S, 2007. Establecimiento de seis especies arbóreas nativas en un pastizal degradado en La Selva Lacandona, Chiapas, México. Ecol Apl 6: 1-8. https://doi. org/10.21704/rea.v6i1-2.335 Román-Dañobeytia FJ, Levy-Tacher SI, Aronson J, Rodrigues RR, Castellanos-Albores J, 2012. Testing the performance of fourteen native tropical tree species in two abandoned pastures of the Lacandon rainforest region of Chiapas, Mexico. Restor Ecol 20: 378-386. https://doi.org/10.1111/j.1526-100X.2011. 00779.x Sabogal C, Guariguata MR, Broadhead J, Lescuyer G, Savilaakso S, Essoungou JN, Sist P, 2013. Manejo forestal de uso múltiple en el trópico húmedo; oportunidades y desafíos para el manejo forestal sostenible. FAO Forest Paper 173, Roma/ Centro Internacional de Investigación Forestal, Bogor, Indonesia. Salisbury CL, Potvin C, 2015. Does tree species composition affect productivity in a tropical planted forest? Biotropica 47: 559-568. https://doi.org/10.1111/ btp.12252 Serrada-Hierro R, 2008. Apuntes de selvicultura. Servicio de Publicaciones EUIT Forestal, Univ Politécnica, Madrid, Spain. Silva PSL, Holanda AER, Paiva HND, Oliveira FHTD, Oliveira OFD, 2012. Planting density and initial growth of two tree species adapted to the semi-arid region. Rev Árvore 36: 951-960. https://doi.org/10.1590/ S0100-67622012000500017 Valverde-Otárola JC, Arias D, 2020. Efectos del estrés hídrico en crecimiento y desarrollo fisiológico de Gliricidia sepium (Jacq.) Kunth ex Walp. Colomb For 23: 20-34. https://doi.org/10.14483/2256201X. 14786 van Breugel M, Hall JS, Craven DJ, Gregoire TG, Park A, Dent DH, et al., 2011. Early growth and survival of 49 tropical tree species across sites differing in Forest Systems April 2022 • Volume 31 • Issue 1 • e003 9 Tree species for reforestation in a tropical coastal area soil fertility and rainfall in Panama. Forest Ecol Manag 261: 1580-1589. https://doi.org/10.1016/j.foreco.2010.08.019 Villanueva-López G, Martínez-Zurimendi P, Casanova-Lugo F, Ramírez-Avilés L, Montañez-Escalante PI, 2015. Carbon storage in livestock systems with and without live fences of Gliricidia sepium in the humid tropics of Mexico. Agrofor Syst 89: 1083-1096. https://doi.org/10.1007/s10457-015-9836-4 Villanueva-Partida CR, Casanova-Lugo F, González-Valdivia NA, Villanueva-López G, Oros-Ortega I, Cetzal-Ix W, Basu SK, 2019. Traditional uses of dispersed trees in the pastures of the mountainous region of Tabasco, Mexico. Agrofor Syst 93: 383-394. https:// doi.org/10.1007/s10457-017-0125-2 Weaver PL, Schwagerl JJ, 2008. Secondary forest succession and tree planting at the Laguna Cartagena and Cabo Rojo wildlife refuges in southwestern Puerto Rico. AMBIO: J Hum Environ 37: 598-603. https:// doi.org/10.1579/0044-7447-37.7.598 Wishnie MH, Dent DH, Mariscal E, Deago J, Cedeño N, Ibarra D, et al., 2007. Initial performance and reforestation potential of 24 tropical tree species planted across a precipitation gradient in the Republic of Panama. Forest Ecol Manag 243: 39-49. https://doi.org/10.1016/j.foreco.2007.02.001