Research Article
Research Article
Plant species diversity and composition in limestone forests of the Vietnamese Cat Ba National Park
expand article infoVan Vien Pham§, Christian Ammer§, Peter Annighöfer|, Steffi Heinrichs§
‡ Forestry Faculty, Northeast College of Forest and Agriculture, Quangninh, Vietnam
§ Georg-August-University Göttingen, Göttingen, Germany
| Technical University of Munich, Munich, Germany
Open Access


Plant species diversity and composition play crucial roles in many ecosystem services and are largely influenced by environmental conditions, as well as natural and/or anthropogenic disturbances. However, our knowledge of the drivers of plant species diversity and composition in the limestone forests of Vietnam, a hotspot of biodiversity, is limited. To fill this knowledge gap, we surveyed plant species in the Cat Ba National Park (CBNP), located on a limestone archipelago. We hypothesised that: (1) topography, accessibility and spatial isolation drive the diversity and composition of plant communities in the CBNP and that (2) isolated areas contribute to high floristic regional diversity by supporting unique species assemblages. We expected high tree species diversity within the tropical limestone forests of the CBNP, but also that: (3) the abundance of non-tree species negatively affects tree regeneration diversity and abundance. Data were obtained from 90 random sample plots (500 m2) and 450 sub-sample plots (25 m2) in three areas of the CBNP. We differentiated four different plant species communities and found a total of 302 species belonging to 112 families. Tree species contributed 50% to total species richness. The distribution of different plant communities in the CBNP was driven mainly by topography; that is, the percentage of rock surface and slope and concomitant differences in soil depth. Contrary to our expectations, isolated areas did not contribute greatly to the CBNP’s plant species diversity. It seems that isolated areas and, as in our case, rough topography, may act as natural barriers to seed dispersal, creating an environmental filter for tree species. Across the CBNP, there was no effect of non-tree species on tree species regeneration, but regeneration patterns differed between communities. In species-rich communities growing under favourable site conditions (e.g. low rock surface and slope), greater coverage by non-tree species had an increasingly negative effect on tree species richness and abundance in the regeneration layer. The opposite was observed in communities growing under harsh site conditions. We conclude that plant species diversity in the CBNP is high, particularly in easily accessible lowland areas where tree species contribute greatly to biodiversity. However, here, non-tree species can even restrict tree regeneration.


Gamma diversity, heterogeneity-diversity relationship, plant species community, plant species diversity


Plant species diversity and composition are important drivers of forest ecosystem functions and services. They provide habitat and resources for different taxonomic groups and food resources (e.g. fruits) for humans (Trejo and Dirzo 2002; Behera and Misra 2005; Seta et al. 2018). Plant species richness and species co-existence in forests are influenced by topography, soil characteristics and climate variables (temperature and precipitation parameters), as well as habitat heterogeneity and habitat size (Wright 2002; Bailey et al. 2010). In addition, natural and anthropogenic disturbances can contribute both to biodiversity gain and loss and to changes in species composition (Behera and Misra 2005; Mendes et al. 2016). Each forest type has unique characteristics in terms of both plant species diversity and its most important drivers. Thus, studies of distinct forest types and forest configurations can reveal new and unexplored patterns.

According to one fundamental ecological theory, environmental heterogeneity is crucial for the diversity, distribution and growth of plant species communities (Hutchinson 1957; Trichon 1997; Vivian-Smith 1997; Holl et al. 2013); differences in soil nutrients (Tateno and Takeda 2003; Yavitt et al. 2009) or micro-topographic variation (Trichon 1997; Vivian-Smith 1997; Tateno and Takeda 2003) lead to niche differentiation, inducing species co-existence. Plant species diversity also depends on habitat configuration, including geographic isolation or fragmentation (Quinn and Harrison 1988; Martin-Queller et al. 2017; Uhl et al. 2021). Isolated habitats can be characterised by distinct habitat conditions with a high diversity of specialised species (Quinn and Harrison 1988; Martin-Queller et al. 2017; Uhl et al. 2021). In contrast, Scheffer et al. (2006) found a negative effect of small habitat size and isolation on the biodiversity of shallow lakes and ponds in Britain due to limitations in habitat size, degree of connectivity and dispersal. In other studies, it was found that half of the native plant species richness was lost in small mixed dipterocarp forest fragments after a century of isolation (Turner et al. 1996). Therefore, the impact of isolation or fragmentation on plant species richness at local and regional scales must be explored in more detail for different forest types. This may be especially important for forest landscapes that are characterised by natural barriers, such as steep slopes and ridges or water bodies in island landscapes.

In addition to species diversity, interactions amongst vertical forest layers are important for forest development and functioning. The overstorey layer affects the understorey primarily via canopy cover (Berger and Puettmann 2000; Prieto et al. 2014) and litter quality (Zhang et al. 2010; Tsai et al. 2018). The overstorey layer provides favourable habitats for, for example, ferns, lianas, epiphytes, herbs and epiphyllous organisms (Mezaka et al. 2020). The understorey contributes to the total species diversity of a forest ecosystem (Linares-Palomino et al. 2009) and affects soil properties, evaporation and humidity. Tree species regeneration as part of the understorey influences the composition and structure of the overstorey layer over the long term (Fang et al. 2014; Thrippleton et al. 2018; Pham et al. 2020). Understorey plant species assemblages may compete with tree regeneration for water, nutrients and light or may facilitate regeneration by, for example, protecting small trees from browsers (Nuttle et al. 2013). However, the relationship between overstorey and understorey depends on the forest type and on environmental conditions and may, therefore, vary with landscape heterogeneity (Laska 1997; Tardella et al. 2017) or with the impact of former (natural or anthropogenic) disturbance history.

Tropical and subtropical forests are known as remarkably diverse ecosystems and are considered biodiversity hotspots (Fangliang et al. 1997; Both et al. 2011). Their immense species richness makes complete sampling coverage difficult and underscores the importance of every study’s contribution to the characterisation of the diversity of these forest ecosystems (Cicuzza et al. 2013). Plant species diversity and composition also play important roles in socio-economics, environmental protection and the living conditions of people who depend on forests and their products, especially in tropical forests of Southeast Asia (including Vietnam; Sodhi et al. 2009; Sun et al. 2009). In Vietnam, 11,373 plant species, belonging to 2,524 genera, 378 families and seven phyla have been identified; these include many species important for medical use (FSIV 2009). In 2006, the forested area was 12,874 million ha (38% forest cover) comprising of 10,410 million ha of natural forests and 2,464 million ha of plantations (FSIV 2009). In addition, the Vietnamese government has established 30 national parks and protected areas to protect and preserve precious genetic resources within natural forests (Pham and Nguyen 2018). To date, floristic research in Vietnam has concentrated on a few national parks, nature reserves and forest types. Here, we focused on the Vietnamese Cat Ba National Park (CBNP). This study aims to increase our knowledge of plant species diversity and the distribution of plant species in limestone forests of Vietnam, a forest type poorly studied up until now. The CBNP is located on a limestone archipelago and differs greatly from the mainland national parks of Vietnam in having many isolated islands and valleys and it is not known how this landscape configuration contributes to the plant species diversity and composition of the National Park or if the configuration affects the relationship between the overstorey and the understorey vegetation including tree regeneration. By surveying plant species in three different study sites of the CBNP representing in total ca. 4,000 ha, we hypothesised that; (1) topography, accessibility and spatial isolation are the main drivers of differentiation amongst plant communities in the CBNP. Further, we assumed that: (2) isolated areas contribute to high floristic regional diversity of the CBNP by supporting unique species assemblages. We also expected high diversity of tree species, but also that: (3) the abundance of non-tree species can negatively affect tree regeneration diversity and abundance. We assumed that this negative effect would be greater in habitats characterised by adequate water and nutrient availability by inducing competition (Holmgren et al. 1997). A negative effect of the understorey on tree species regeneration could influence tree species diversity of the CBNP in the long term.

Our study aims to contribute to the knowledge of the autecology of different plant species and plant species assemblages within limestone forests of Vietnam as a potential basis for future monitoring and conservation programmes.


Study site

The CBNP is situated on Cat Ba Island, in the Tonkin Gulf, northern Vietnam. It lies ca. 45 km east of Haiphong City and 150 km south-east of Hanoi. Geographical coordinates are 20°44'N to 20°55'N (DM), 106°54'E to 107°10'E (DM) (Fig. 1) (Pham et al. 2020).

Figure 1.

Location of Cat Ba National Park (CBNP), Haiphong, Vietnam. We collected data at three different study sites: MSA, a mid-slope area; LLA, a lowland area; ISA, an isolated area; 4, 5 and 6 are other restricted areas in the CBNP that were not considered for this study (Pham et al. 2020). Map data copyrighted by OpenStreetMap contributors and available from (CC BY-SA 2.0).

The CBNP is located on a limestone archipelago that consists of 366 islands and islets (CBNP 2005). The total CBNP area is 16,197 ha with ca. 10,932 ha of terrestrial island areas and 5,265 ha of marine areas (CBNP 2005, 2007). The average elevation is between 100 and 150 m a.s.l. with the highest peak of 331 m a.s.l. and average slopes ranging from 15° to 35° (CBNP 2007). The CBNP is characterised by two distinct seasons: the rainy season (from May to October) and the dry season (from November to April) with yearly rainfall from 1,500 to 2,000 mm. Average annual temperature is 23 °C and the average air humidity is approximately 86% (CBNP 2005; Le 2006).

Various ecosystems and forest types can be found in the CBNP and these include evergreen forests on limestone, wetland forest ecosystems in steep mountain valleys, mangrove forests, coral reefs and cave systems (CBNP 2005; Le 2006). The forest ecosystems include primary (undisturbed by direct human activity) evergreen broadleaf tropical rain forests, secondary evergreen broadleaf tropical forests in the lowlands (previously disturbed by human activity) and on limestone mountains, secondary moist evergreen restoration forests on limestone mountains and valleys, restored bamboo forests, wetland forests in the limestone valleys, mangrove forests and plantation forests (Carle and Holmgren 2003; CBNP 2007).

In 2004, Cat Ba Island was designated a UNESCO biosphere reserve because of its diverse flora and fauna (CBNP 2005). In total, 1,561 vascular plant species belonging to 842 genera and 186 families have been recorded across the different terrestrial ecosystems. Amongst them, 408 tree species have been observed in the CBNP in the past years by local authorities (CBNP 2007). Twenty-nine tree species listed in the IUCN Red List were recorded in the CBNP (Le 2006; CBNP 2007). Forty-three additional tree species are listed on the Vietnam Red List in terms of conservation (Le 2006; CBNP 2007). To allow the natural development of ecosystems and to protect precious plants and animals in the CBNP, six strictly protected zones were established, totalling 4,915 ha (Fig. 1). In these protected areas, management activities, such as timber logging, hunting or slash and burn, are prohibited. We chose three of the six restricted areas for our study that represent the three main conservation areas of the National Park. These three areas are characterised by primary and secondary evergreen broadleaf tropical forest ecosystems (Fig. 1). These areas also represent an accessibility gradient. The lowland area (LLA) (1,916.4 ha) is in the centre of the Park and is the most easily accessible of the three. The mid-slope area (MSA) (600 ha) lies in the north-western part of the Park and is characterised by steeper slopes compared to the LLA. The third area is an isolated area (ISA) (1,557.8 ha) and is located on a separate island in the eastern part of the Park. Its island situation isolates ISA from the two other study areas (Fig. 1). Note that in Fig. 1, some local villages were included into the boundaries of MSA, making the study area larger than the actual forested area.

Data sampling

We used the simple random sampling technique (Kleinn et al. 2009) to set up sample plots (Fig. 2). Thirty strips were created in each research area. In each strip, random sample plots were generated using random numbers to determine their coordinates. Two uniform random numbers U1i, U2i (the U interval from 0 to 1) were used each time to calculate Xi = U1i * Xmax, with Yi = U2i * Ymax as coordinates for each random sample plot, where Xmax and Ymax were the largest coordinates of the area map (Fig. 2). If the coordinate (Xi, Yi) appeared within the defined strip, this point was accepted as a sample plot point. Otherwise, the point was rejected and the procedure was repeated with two new U(s) random values (Fig. 2).

Figure 2.

Sampling design scheme.

Based on this technique, a total of 90 random sample plots were created (30 plots in each of the three protected areas (LLA, MSA and ISA)). Each sample plot area was 500 m2 in size (20 m × 25 m).

Overstorey tree layer

Within each sample plot, diameter at breast height (DBH) and height of all overstorey trees with DBH ≥ 5 cm were measured. We identified each individual tree to the species level. We defined species of the overstorey tree layer as tree species that now or in the future will be able to form the upper forest canopy. Botanists of the Northeast College of Agriculture and Forest (AFC) and from Cat Ba National Park assisted with identification. All recorded tree species were assigned to categories of threat according to the IUCN Red List categories (IUCN 2017).

Regeneration layer

We assigned individual trees, potentially able to reach the upper canopy in the future, with DBH < 5 cm to the regeneration layer. Regeneration was recorded on five subplots, which were established on five positions within each sample plot (Fig. 2) (Pham et al. 2020). Each subplot area was 25 m2 (5 m × 5 m). Seedlings and saplings of all tree species were identified to the species level. Tree species found in the regeneration layer were also assigned to categories of threat following the approach for standing tree species.

Non-tree species layer

We additionally assigned plant species, other than trees and irrespective of their height, to the forest understorey and identified them to species level. We defined this layer as the non-tree species layer. Species included shrubs (even > 5 cm DBH), bamboo species, vines, medical plants and edible plants (MARD 2006; Sorrenti 2017). The non-tree species were recorded in the five subplots (Fig. 2) by estimating their coverage percentage. Coverage from all five subplots was then averaged to determine per plot coverage.

Growth site conditions

To characterise the growing conditions of plant species in the different plots and study areas, we recorded variables describing topography, soil conditions and light availability, as well as former impacts by humans.

As topographic variables (T), we recorded slope (T_SL), elevation (T_Ele) and percentage of rock surface area (T_RS) per sample plot. At the centre of each sample plot, the slope was measured with an inclinometer. Longitude, latitude and elevation were measured with a Garmin GPSMAP 64st device. A visually estimated mean value of rock exposure across the five subplots resulted in values for rock surface area (T_RS) per plot (%).

Soil conditions (S) included chemical and physical properties. Soil samples were collected at the centre of each sample plot using a soil auger (diameter 10 cm). A 20 cm core of the topsoil layer was sampled to analyse absolute soil moisture content (S_SM), soil humus content (S_SH), base saturation (S_BS), pH (S_pH), hydrolytic acidity (S_HA), total cation exchange capacity (S_CEC), soil texture (S_Sand, S_Silt, S_Clay) and percentage of rock in soil (S_RS). Soil depth (S_SD) was measured with a steel rod on the five subplots; the five values were then averaged. Samples were analysed in the soil laboratory of the Vietnam National University of Forestry. For details, see Pham et al. (2020) and Pham et al. (2022).

Light availability (L) was measured with a solariscope (SOL 300B, Ing.-Büro Behling, Wedemark) as an indirect site factor (L_ISF), which is the proportion of diffuse sunlight as a percentage of open field conditions. Measurements were conducted at 2 m above the ground on three diagonal subplots across the sample plot (Fig. 2).

After its establishment in 1986, the board of directors of the CBNP tried to reduce the human impact in the core zones of the CBNP by moving people outside the core zones. To date, however, many villages are still located close to the CBNP. Hence, activities of the local people, such as illegal logging and hunting, can still be detected. To roughly quantify a possible human impact (H), we counted footpaths (H_FP), tree stumps (H_STP) and poacher traps to catch animals (H_AT) on the plots as proxies for human activities.

Data analysis

To analyse plant species composition in the CBNP and to identify different forest communities, we used hierarchical cluster analysis with Ward’s method using the function ‘vegdist()’ to create a Bray Curtis distance matrix, the function ‘hclust()’ to conduct a cluster analysis and the function ‘cutree()’ to draw a community dendrogram. These functions are implemented in the ‘vegan’ package in R (Oksanen et al. 2019).

To display the spatial distribution of communities in multidimensional space, we used the non-metric multidimensional scaling (NMDS) ordination method, based on abundance data. In the first step, we used the ‘metaMDS()’ function to run an NMDS and then used the ‘envfit()’ function to add environmental data into the NMDS graph using ‘vegan’ in R . We included all vegetation layers into the NMDS. Tree species of the overstorey and regeneration layers were combined to avoid duplication of species names.

To determine indicator species for identified forest communities, we used the function ‘multipatt()’ in the package ‘indicspecies’ (De Cáceres and Legendre 2009). The indicator species analysis calculates the specificity of a species as the number of occurrences of a species within a community relative to the number of occurrences across communities and the frequency of the species within a community as the relative number of occurrences per community. Multiplying specificity and frequency results in an indicator value between 0 (species not occurring in a specific forest community) and 1 (species occurring only and always in a specific community). The most significant indicator species identified amongst the tree and non-tree species were used to name the forest communities that were determined by cluster analysis.

To determine factors affecting community distribution in the CBNP, we correlated the NDMS axes’ values with the environmental factors and human impact indicators. The function ‘anova()’ following a post-hoc Tukey-test with function ‘glht()’ in ‘multcomp’ package was used to compare these variables amongst communities.

We additionally applied different selection operators to build decision trees to weigh the predictors that characterised plant species communities (= the response). Forward selection of the predictors performed best. This method starts with an empty model and adds predictors to explain the response. Performance is estimated in each round using cross-validation. Only predictors with the highest performance increase are kept, then a new round is started. The maximum number of attributes to add was limited to seven to avoid overfitting; the iteration was aborted when performance no longer increased. This yielded a decision tree classifying the plant species communities. Classification trees represent a robust, non-parametric, binary procedure that partitions variance in the variation of communities through a series of splits in more homogeneous groups based on environmental factors or human impact variables (De’ath and Fabricius 2000; Cutler et al. 2007).

We contrasted plant species richness amongst the detected forest communities, species groups (tree and non-tree-species) and vegetation layers (overstorey tree, regeneration, non-tree layer) at different spatial scales. For alpha diversity, we compared plot-based species richness amongst communities using the ‘anova()’ function, followed by a post-hoc Tukey-test with function ‘glht()’ in the ‘multcomp’ package. To compare total species diversity in the identified communities, we used the ‘iNEXT’ package in R (Hsieh et al. 2016) to estimate the respective gamma diversity. The ‘iNEXT’ package applies different orders of Hill numbers (q) and quantifies diversity by applying rarefaction and extrapolation methods (Chao et al. 2014). We considered the first three Hill numbers referring to species richness (q = 0), the true diversity of the Shannon Index, which is the exponential of the Shannon Index (q = 1) and Simpson diversity (q = 2) (Chao and Jost 2012; Hsieh et al. 2016). We estimated diversity for each defined forest community separately and across communities as an estimate for the gamma diversity of the CBNP.

To investigate how much each detected forest community contributed to the gamma diversity of the CBNP, we contrasted the estimated species pool of different combinations of communities to the species pool estimated for a combination of all detected communities. We also estimated the gamma diversity of tree and non-tree species of the CBNP and of different forest communities.

The relationship between non-tree species and the overstorey tree layer and between non-tree species and the regeneration layer was checked using linear regression models. We investigated the relationships across communities and for each community separately.

All statistical analyses were conducted using the statistical software R version 3.4.2 (R Core Team 2017). The level of significance for all statistical inferences was defined as p-value < 0.05.


Forest communities of the CBNP

We identified four main communities that differ distinctly in species composition in Cat Ba National Park, (Fig. 3, Appendix 1). Each community has characteristic indicator species (Table 1). The most reliable indicators (highest indicator index value) amongst the tree and non-tree species provided the community names (Table 1, species characteristics are provided in Appendix 2). We defined the Saraca dives + Calamus tetradactylus community (SCt), the Sterculia lanceolata + Chloris barbata community (SCb), the Ficus superba + Acanthus ebracteatus community (FAe) and the Clausena excavata + Desmos cochinchinensis community (CDc) (Appendix 2). Most indicator species (14 species) were associated with the SCt community, six species were associated with the SCb community and only four indicator species with the FAe community. For the CDc community, ten indicator species were identified (Table 1).

Table 1.

Indicator species of the four identified forest communities. The eponymous tree and non-tree indicator species are given in bold. The growth form of each species is given as species group. See Appendix 8 for a list of all species detected within the study plots.

Species Species group Indicator value p-value
Saraca dives + Calamus tetradactylus community (SCt)
Saraca dives Tree 0.789 0.001
Calamus tetradactylus Vine 0.681 0.001
Peltophorum pterocarpum Tree 0.630 0.001
Ardisia gigantifolia Shrub, medical plant 0.592 0.001
Garcinia oblongifolia Tree 0.582 0.002
Gomphandra tonkinensis Shrub, medical plant 0.496 0.002
Cinnamomum ovantum Tree 0.469 0.011
Bauhinia coccinea Shrub 0.445 0.008
Aglaia spectabilis Tree 0.444 0.013
Ardisia silvestris Shrub, medical plant 0.417 0.007
Mussaenda crosa Shrub 0.401 0.014
Phoebe pallida Tree 0.373 0.041
Caryota obtusa Shrub 0.369 0.037
Phytele phantoideae Shrub 0.369 0.034
Sterculia lanceolata + Chloris barbata community (SCb)
Sterculia lanceolata Tree 0.694 0.001
Paramichelia baillonii Tree 0.520 0.002
Zanthoxylum nitidum Tree 0.500 0.001
Chloris barbata Grass 0.423 0.003
Convolvulus parviflorus Shrub 0.380 0.044
Markhamia cauda-felina Tree 0.378 0.035
Ficus superba + Acanthus ebracteatus community (FAe)
Acanthus ebracteatus Shrub 0.931 0.001
Ficus superba Tree 0.418 0.009
Bursera tonkinensis Tree 0.401 0.049
Connarus paniculatus Vine 0.387 0.013
Clausena excavata + Desmos cochinchinensis community (CDc)
Clausena excavata Tree 0.800 0.001
Microcos paniculata Tree 0.775 0.001
Desmos cochinchinensis Vine 0.644 0.001
Zephyranthes carinata Herb 0.541 0.002
Helixanthera parasitica Shrub 0.468 0.015
Pandanus tectorius Shrub 0.448 0.008
Blumea lacineata Herb 0.402 0.024
Syzygium jambos Tree 0.400 0.032
Morinda citrifolia Tree 0.387 0.017
Cnestis palala Vine, medical plant 0.374 0.049
Figure 3.

Spatial distribution of communities in NMDS analysis. The ellipses show the confidence levels at 95% of covariance of each community.

Ordination revealed that the SCt community was found mainly in the lowland area (LLA). The SCb community characterised a transition from the lowland to mid-slope area. The FAe community was associated with the mid-slope area and the CDc community with the isolated area (Fig. 3).

Forest structure and abiotic conditions of the forest communities

Forest structure differed amongst the four communities. On average, we found the lowest diameter at breast height (DBH), height (Ht), basal area (BA) and volume (Vol) in the FAe community, while the SCt community was characterised by the highest mean volume, DBH, basal area and height. The SCb community had the highest tree species richness, whereas the CDc community was the most species-poor in the overstorey layer (Table 2).

Table 2.

Forest structure of the different forest communities in the CBNP. The highest and lowest values are written in bold. Different letters indicate statistically significant differences amongst communities.

SCt community SCb community FAe community CDc community
DBH (cm) 24.1 ± 4.47c 22.1 ± 5.22b 18.5 ± 4.83a 22.1 ± 3.68b
Ht (m) 12.58 ± 2.23c 10.68 ± 1.52b 9.32 ± 1.9a 10.52 ± 1.47b
BA (m2.ha-1) 36.4 ± 17.0c 29.1 ± 19.7b 21.1 ± 15.5a 27.8 ± 11.5b
Vol (m3.ha-1) 279.23 ± 160c 229.27 ± 193b 163.06 ± 157a 209.51 ± 108b
Tree species richness 15.4 ± 6.1b 15.5 ± 6.0b 13.4 ± 2.8a 12.9 ± 2.6a

Community comparisons, as well as the decision tree analysis, showed that the communities FAe and CDc were associated with steeper slopes and a high percentage of rock surface area (Fig. 4, Table 3, Appendix 3). In contrast, the SCb and SCt communities were found in areas with deeper soils (Fig. 4, Table 3, Appendix 3). Although soils are shallower in the habitats of the FAe and CDc communities, their soil humus content (S_SH), soil moisture (S_SM) and cation exchange capacity (S_CEC) were high (Fig. 4, Table 3, Appendix 3) in the upper soil layers. Light conditions differed little between the four communities. Overall, SCb received the most light (Table 3, Appendix 3). Indicators of human impact were mainly associated with the communities SCt and SCb (Fig. 4).

Table 3.

Mean values (± standard deviation) of environmental and human impact factors of the four communities. Superscript letters indicate statistically significant differences amongst the four communities. The highest and lowest values for each variable are written in bold.

Indicators SCt community SCb community FAe community CDc community
Number of sample plots 22 28 20 20
T_SL (Slope) (°) 11.7 ± 8.77a 14.4 ± 9.44b 26.1 ± 10.82d 22.3 ± 8.42c
T_RS (Rock surface) (%) 20 ± 17.1a 35.6 ± 23.1b 71.9 ± 19.3d 81.9 ± 12.6c
T_Ele (Elevation) (m) 74 ± 31.9b 62.7 ± 35.7a 87.2 ± 42.7c 89.1 ± 42.8c
S_SD (Soil depth) (cm) 79.8 ± 39.0c 76.5 ± 34.0b 32.3 ± 17.9a 34.6 ± 23.9a
S_SR (Rock in soil) (%) 12.98 ± 23.05c 8.74 ± 14.85b 8.53 ± 6.17b 5.83 ± 2.96a
S_SM (Soil moisture) (%) 5.76 ± 5.5a 8.24 ± 5.2b 14.12 ± 3.9d 13.24 ± 3.3c
S_Sand (Sand content) (%) 31.5 ± 10.9c 29.8 ± 11.6b 25.2 ± 10a 38.6 ± 16.6d
S_Clay (Clay content) (%) 27.1 ± 11.19a 28.8 ± 7.88b 33.8 ± 5.99b 27.5 ± 9.21a
S_SH (Soil humus content) 2.8 ± 1.47b 2.46 ± 1.02a 3.91 ± 1.58c 4.59 ± 1.02d
S_pH (pH value) 4.77 ± 0.52a 5.10 ± 0.52b 5.58 ± 0.46d 5.47 ± 0.28c
S_HA (Soil acidity) 5.20 ± 2.23b 4.57 ± 1.72a 4.73 ± 1.74a 5.39 ± 2.47b
S_BS (Base saturation) (%) 55.5 ± 13.05a 59.9 ± 10.82b 63.7 ± 10.22d 61.9 ± 9.09c
S_CEC (Cation exchange capacity) 6.13 ± 1.47a 6.63 ± 1.30b 8.07 ± 1.20c 8.28 ± 0.80d
H_FP (Footpaths) (N.plot-1) 1.27 ± 0.45c 1.26 ± 0.49c 1.07 ± 0.53b 1.00 ± 0.0a
H_Stp (Stumps) (N.plot-1) 0.16 ± 0.37b 0.15 ± 0.36b 0.0 ± 0.0a 0.0 ± 0.0a
H_AT (Animal traps) (N.plot-1) 0.62 ± 1.38b 1.01 ± 1.79d 0.78 ± 1.56c 0.43 ± 1.12a
L_ISF (Indirect site factor) (%) 8.80 ± 2.96b 9.56 ± 8.81c 8.12 ± 2.15a 9.22 ± 3.30bc
Figure 4.

Correlation of environmental and human impact factors if significant (T = topographic variables, S = soil variables, H = human impact) with the NMDS axes. Length of the arrow indicates the strength of the correlation. Arrows in the same direction indicate a positive correlation of the variables with each other and a unidirectional response to NMDS axes. All variables that significantly correlated with the axes (p-value < 0.05) are shown. ISA = isolated area; LLA = lowland area; MSA = mid-slope area. The abbreviations for environmental and human disturbance factors are defined in Table 3.

Differences in environmental factors among communities were also reflected in the differences in environmental factors among the study sites in which the communities were mainly located (see Figs 3, 4, Appendices 1, 4). For example, the average slopes in ISA and MSA were steeper than in LLA. As the FAe and CDc communities were associated mainly with the MSA and ISA sites, they were also characterised by higher slope values compared to the other two communities (Appendix 1). In addition, the ISA site had the highest percentage of rock surface as did the CDc community (Appendix 3).

Patterns of plant species diversity of the forest communities

Across communities, the non-tree species layer was, on average, more species-rich than the overstorey and regeneration layers, with the highest non-tree species richness found in the SCb community (Fig. 5). The overstorey tree layer was significantly more diverse in the SCt and SCb communities compared to the FAe and CDc communities (Fig. 5). A similar pattern was found for the regeneration layer (Fig. 5). Thus, the communities with the lowest plot-based species richness of the regeneration layer also had the lowest plot-based species richness in the overstorey tree layer.

Figure 5.

Boxplots of species richness of the three investigated layers in each forest community. Letters indicate statistically significant differences amongst communities. SCt; Saraca dives + Calamus tetradactylus community. SCb; Sterculia lanceolata + Chloris barbata community. FAe; Ficus superba + Acanthus ebracteatus community. CDc; Clausena excavata + Desmos cochinchinensis community.

Gamma diversity estimations identified significantly higher values for the communities SCt and SCb compared to the communities FAe and CDc. For the Hill number q = 2, the SCb community, which characterised the transition from the lowland to the mid-slope area, was significantly more diverse than the other three communities; confidence intervals do not overlap. For all Hill numbers, the forest community associated mainly with the isolated area (CDc) had the lowest gamma diversity (Fig. 6). When plots of all four communities were combined, gamma diversity did not exceed the most diverse community, indicating that community assemblages are not complementary, but exhibit nested diversity.

Figure 6.

Estimated gamma diversity for different Hill numbers and forest communities. q = 0: species richness; q = 1: Shannon diversity; q = 2: Simpson diversity. The red colour represents the estimated gamma diversity when all communities are considered for estimation. Yellow-green: Saraca dives + Calamus tetradactylus community (SCt). Green: Sterculia lanceolata + Chloris barbata community (SCb). Light-blue: Ficus superba + Acanthus ebracteatus community (FAe). Pink: Clausena excavata + Desmos cochinchinensis community (CDc). Graphs were extrapolated to a sample size of 90 plots.

When investigating the importance of each community to CBNP gamma diversity, we first estimated the species pools of different combinations of communities. We found that the SCb and SCt communities were most important for regional gamma diversity. When these communities were eliminated from community combinations, gamma diversity was greatly reduced as compared to the total species pool and to other community combinations (Appendix 5). If, however, the CDc and FAe communities were not included in the estimation procedure, the estimated species pool was not significantly different from the total species pool, indicating that these communities are mainly subsets of the species-richer communities (Appendix 5).

Gamma diversity patterns of the different communities were driven in large part by tree species (Fig. 7). Tree species were significantly less diverse in the communities FAe and CDc compared to the other two communities (Fig. 7, Appendix 6). For the non-tree species, the difference between the two community groups (SCb, SCt vs. FAe, CDc) was not as pronounced for q = 0 (Fig. 7). For q = 1, the SCb community was significantly more diverse than the communities FAe and CDc. For q = 2, SCb was more diverse than all other identified communities (Fig. 7, Appendix 6).

Figure 7.

Gamma diversity patterns of tree species and non-tree species of the different communities. The graphs show species richness (Hill number q = 0, including 95% confidence interval). Red: all four communities, Yellow-green: Saraca dives + Calamus tetradactylus community (SCt), Green: Sterculia lanceolata + Chloris barbata community (SCb), Light-blue: Ficus superba + Acanthus ebracteatus community (FAe), Pink: Clausena excavata + Desmos cochinchinensis community (CDc). For Hill numbers q = 1 and q = 2, see Appendix 6. Graphs were extrapolated to a sample size of 90 plots.

Tree and non-tree species contributed nearly equally to the diversity of the CBNP (Table 4). However, in the SCt and SCb communities, tree species diversity was higher than non-tree species diversity, while in the other two communities, the converse was true (Table 4).

Table 4.

Estimated species pool by species group and community for q = 0. The value in brackets indicates the 95% confidence interval.

Layer All communities SCt community SCb community FAe community CDc community
All species 367.7 316.7 317.0 211.4 178
(339.3 ÷ 417.7) (261.6 ÷ 415.5) (275.5 ÷ 391.5) (178.2 ÷ 275.8) (146.4 ÷ 249.3)
Tree species 190.8 190.5 175.7 87 73.2
(170.4 ÷ 235.0) (144.7 ÷ 290.7) (140.7–253.4) (75.6–118.1) (61.4 ÷ 110.7)
Non-tree species 177.6 130.2 145.7 133.1 110.6
(161.9 ÷ 212.4) (105.0 ÷ 189.0) (126.2–190.5) (98.9 ÷ 214.6) (80.5 ÷ 199.4)

Relationships between vertical forest layers

We did not find a significant relationship between species richness of the non-tree layer and that of the tree regeneration layer. We also found no effect of species richness of the overstorey tree layer on species richness of the non-tree species layer or the regeneration layer (Fig. 8).

Figure 8.

Linear regression models of plot-based species richness relating: a species richness of the non-tree species layer and species richness of the regeneration layer b species richness of the overstorey tree layer and species richness of the non-tree species layer and c species richness of the overstorey tree layer and species richness of the regeneration layer. The shaded area indicates the 95% confidence interval.

Across all communities, there was also no significant effect of the coverage of the non-tree species layer on the species richness or abundance of the regeneration layer (Fig. 9a, c). However, at the community level, we found that coverage of the non-tree species layer negatively affected both abundance and richness of the regeneration layer in the SCb community and of richness in the SCt community. In contrast, coverage by the non-tree species layer positively influenced the richness of the regeneration layer in the FAe community (Fig. 9b, d).

Figure 9.

Linear regression models of the coverage of non-tree species and species richness and abundance of the tree regeneration layer. Graphs (a) and (c) show the relationship between the coverage of non-tree species with the abundance and species richness of tree regeneration across all communities, graphs (b) and (d) for the four communities. Dashed lines show statistically non-significant, solid lines show significant correlations. To improve visibility, we did not include the confidence intervals for (b) and (d).

We did not observe any significant effect of species richness or coverage of the non-tree species layer on tree abundance or richness of threatened tree species in the regeneration layer (Appendix 7).


Topographic heterogeneity drives the spatial distribution of forest communities in the CBNP

We distinguished four forest communities in the CBNP that differ in forest structure and are characterised by different environmental conditions (Fig. 3, Tables 1, 2, Appendix 1). Topographic variables, in combination with soil conditions, turned out to be important factors influencing the differences in plant species composition across the CBNP. Topographic heterogeneity can result in different microclimatic conditions, affecting temperature and soil moisture at small scales, thus influencing the abundance and distribution of plant species (Vivian-Smith 1997; Seta et al. 2018). In addition, topographic heterogeneity indirectly acts on plant species composition and diversity through drainage and by differences in the hydraulic regime, which results in different growing conditions for plants on ridges, slopes and in valleys (Trichon 1997). These characteristics may also affect seed erosion and seed accumulation, leading to differences in plant species distributions (Vivian-Smith 1997; Holl et al. 2013).

We found that the SCt and SCb communities occurred mainly on sites characterised by deep soils, whereas the FAe and CDc communities were found on sites with rough terrain (steep slopes and high rock surface), but with relatively high soil nutrient content (high soil humus content and CEC) (Fig. 4, Table 3, Appendices 1, 4). Our environmental characterisation of the communities corresponded well to the investigated study sites. The SCt and SCb communities characterised the lowland area in transition to the mid-slope study area, while the CDc community was associated mainly with the isolated area, characterised by steep slopes. Our results are in line with Zhang et al. (2021), who identified topography as the main factor determining niche differentiation of tree species in heterogeneous tropical limestone forests of China. Topography influenced soil depth and, thereby, most likely determined water availability and drought stress, factors that may have shaped species distribution.

Topographic heterogeneity can also influence light availability, an important determinant of plant species distribution (Zhu et al. 2016). It also affects forest composition by influencing regeneration patterns (Tateno and Takeda 2003). However, in our case, the indirect site factor (L_ISF), which we used as a proxy for light availability, did not affect plant species distributions (Fig. 4, Table 3, Appendix 4). It is important to mention that the gradient of light availability recorded across our study sites was quite low, indicating a relatively homogeneous canopy cover across the CBNP.

Although indicators of human impact could not be clearly connected to plant species distribution, observed differences in the forest communities of the different study areas could have reflected human influence, which was strongest in the lowland area. In the lowland area, with the communities SCt and SCb, species richness was highest (Figs 4, 5, Table 3). In contrast, other studies found negative effects of human disturbance on species diversity; humans extract certain tree species with subsequent effects on species composition (Blanc et al. 2000; Do et al. 2017). Chazdon (2003), however, concluded that forest recovery could be rapid even after large-scale human disturbances when soil and aboveground vegetation were not heavily impacted. In addition, Dao and Hölscher (2018) found a positive correlation between the occurrence of footpaths and the density of tree species used for non-timber forest products. This suggests a positive effect of human activity on some early-successional species. Other studies have confirmed the strong potential of tropical forests to recover after historical disturbances (Lusk and Smith 1998; Bayliss-Smith et al. 2003), but also underscore the role of historical disturbances, whether anthropogenic or natural, in shaping species composition.

We identified several indicator species for the four forest communities that provided valuable information on species-environment relationships. While species of the communities SCt and SCb seemed to be restricted to deep soils, indicator species in the FAe and CDc were able to tolerate harsh soil conditions, such as a high percentage of rock surface and shallow mineral soils (Guo et al. 2017). They were also able to overcome potential dispersal filters due to the island isolation of the ISA. The bird-dispersed Clausena excavata, for example, is characterised by rapid germination, thereby avoiding the risk of desiccation in shallow soils. High seedling survival under various environmental conditions makes this species both a successful invader outside its native range and a successful coloniser (Vieira et al. 2010). Supporting results by Santo‐Silva et al. (2021) demonstrated that isolation favours the abundance of disturbance-adapted pioneer tree species. The annual herb Blumea lacineata, another indicator in the CDc community, is also characterised by an effective dispersal strategy and is classified as a weed species (Wester 1992). On the other hand, Sterculia lanceolata, an indicator species of SCb, can be characterised as a mid- to late-successional species on deeper soils (Zhang et al. 2013). Its co-existence with the tropical weed species Chloris barbata (Holm et al. 1979) in the CBNP suggests that this community and its assemblage of indicator species characterise a successional stage after disturbance in lowland and mid-slope areas. Lower DBH and tree heights in this community, as compared to the SCt community of the lowlands, support this assumption. The species assemblage of the Saraca dives + Calamus tetradactylus reliably characterises lowland sites, as Saraca dives is a dominant species in foothills and in valleys with high and constant water availability in limestone forests (Zhang et al. 2021).

Thus, our study underscores the value of using identified indicator species or groups of species for an overall assessment of the environmental conditions in tropical limestone forests of Southeast Asia. By monitoring certain indicator species, shifts in environmental conditions can be reliably detected.

Differences in forest community composition do not drive the biodiversity of the CBNP

We identified in total 302 species belonging to 112 families in the CBNP (Table 4, Appendices 5, 8) within the 90 recorded sample plots. The total species pool was estimated at 368 species. We found that, as compared to other studies, plant species diversity in the CBNP was quite high. For example, diversity was higher than that of transitional rainforest vegetation in southwestern Ethiopia (from 130 to 139 species) (Assefa et al. 2013), neotropical primary and secondary forests (100 species found on two 1 ha plots (van Andel 2001), or subtropical forests in China (240 species in 27 plots of up to 900 m2 (Both et al. 2011). It was less diverse, however, than rainforests in Columbia (442 vascular plant species in 0.9 ha; (Galeano et al. 1998) or seasonal dry tropical forests in Mexico (917 species in 20 representative sites of 0.1 ha; (Trejo and Dirzo 2002). Numbers are comparable with forests of Dinagat Island in the Philippines where 432 native plant species have been recorded (Lillo et al. 2019). In Malaysian tropical rain forests, 825 species in 50 ha forest inventory plots have been detected (Fangliang et al. 1997). Although differences in species numbers among the aforementioned studies may also be due to different experimental designs and scales of inventory (Ferraz et al. 2004; Cicuzza et al. 2013; Júnior et al. 2014), our results indicate that plant species diversity in the CBNP is comparable to other tropical and subtropical forests worldwide. Interestingly, non-tree species contributed roughly 50% to total species diversity (Table 4) emphasizing both the importance of different growth forms for biodiversity and confirming other studies (Gentry and Dodson 1987; Linares-Palomino et al. 2009). The forest communities FAe and CDc, characterizing rough and rocky terrain, had a higher share of non-tree species than those of the lowland and mid-slope areas, indicating that this species group is shaped by stochastic assembly processes, while the distribution of tree species is mainly driven by environmental differences among habitats (Both et al. 2011). Similarly, isolation seems to have acted as a stronger barrier for tree than for non-tree species (Hill and Curran 2003; Martin-Queller et al. 2017).

In contrast to our expectations, the heterogeneity we found in forest community composition did not appear to drive overall plant species diversity of the CBNP. The linkage between isolation and species diversity has been investigated in previous studies (Quinn and Harrison 1988; van Andel 2001; Slik et al. 2003; Scheffer et al. 2006; Chytrý et al. 2010). Isolated conditions can promote species diversity and the distinctiveness of communities (Ferraz et al. 2004), and can also drive speciation, leading to species endemism (EI-Bana 2009; Chytrý et al. 2010). Our findings indicate that the isolated area has the lowest species diversity in our study (Figs 6, 7, Appendix 5). This supports the conclusion by van Andel (2001) that relative isolation can also have a negative effect on species diversity. Slik et al. (2003) confirmed that diversity was negatively correlated with isolation and habitat size in North-eastern Borneo forests. Our results, therefore, suggest that rough terrain conditions in combination with the isolated location function as a strong dispersal and establishment filter that only a subset of the plant species can overcome. Such species are characterized by good dispersal ability (see above). The missing complementarity in species diversity among communities, however, indicates that the species assemblages colonizing the isolated area are instead a subset of richer species communities. Species colonizing the isolated sites can therefore be characterized as generalists growing under various site conditions (Vieira et al. 2010; Santo‐Silva et al. 2021).

Our results also confirm the theory that larger areas boost high species diversity. The two species-rich SCt and SCb communities (Figs 3, 6, Table 4, Appendix 5) were located mostly on the main island of the CBNP; this presumably provided more habitats and better habitat connectivity with positive effects on the dispersal ability of species (MacArthur and Wilson 1967; Hill and Curran 2003; Martin-Queller et al. 2017). This agrees with Scheffer et al. (2006), who stated that local diversity is reduced in response to isolation through dispersal limitation. They also implied that larger local habitat patches and greater connectivity facilitate regional biodiversity. Turner et al. (1996) even found that a long period of isolation in lowland tropical forests in Singapore was a major contributor to species loss.

The species-rich SCb and SCt communities were associated with greater soil depth, while the percentage of rock surface and slope were correlated with species-poorer communities (FAe and CDc communities) (Fig. 4, Table 3). Slope and rock outcrops have a huge effect on soil cover in our research areas (Chytrý et al. 2010; Seta et al. 2018), influencing soil nutrients (Chytrý et al. 2010) and water availability (Zhang et al. 2021). This seems not only to result in differences in community composition as discussed before, but also in different numbers of tree and non-tree species. Tree species diversity was more strongly influenced than non-tree species by differences in topography, with more tree species colonizing the lowlands. The Simpson diversity of non-tree species was particularly high in the SCb community. Here the presence of indicator Chloris barbata suggested an impact of former disturbance. We do not have, however, enough information on former anthropogenic or natural disturbance events to make a definitive connection.

Humans can have a huge influence on floristic diversity; there are numerous examples from around the world. For example, Júnior et al. (2014) found that human activities changed tree species diversity and forest structure in semi-deciduous forests in Brazil. Assefa et al. (2013) found that anthropogenic interferences reduced species diversity in southwest Ethiopian forests. In our case, indicators of human impact and species-rich forest communities were positively associated (Fig. 5, Table 2). These results may indicate that the natural recovery potential of a species after historical disturbances is high (van Andel 2001; EI-Bana 2009). In any case, reconstruction of former disturbances would be useful to evaluate the potential for tree species recovery as well as to understand the effects of former disturbances on current species composition. However, as differences in human impact and environmental conditions among communities and study sites interact, we cannot verify a potential impact of former human disturbance on plant species diversity and composition in the CBNP.

Relationship between vertical forest layers

Across communities, we found no interactions amongst forest layers (Both et al. 2011), but found contrasting patterns for the different communities. In the two species-rich communities (SCb and SCt) found on deep soils, we detected negative effects of non-tree species coverage on tree species richness and abundance in the regeneration layer (Figs 8, 9b). It is well known that tree regeneration competes with herbaceous species on sites with sufficient water and nutrient availability (Both et al. 2011). Interestingly, under harsh environmental conditions in the CDc communities and also in the FAe (Fig. 9d), coverage by non-tree species appeared to have neutral (CDc) to positive (FAe) effects on the tree regeneration species richness; this supports the hypothesis that changes in water availability, such as those induced by more shallow soils, can shift plant interactions from competition to facilitation (Bertness and Callaway 1994; Holmgren et al. 1997). Along the steep slopes with high rock coverage, non-tree species can improve conditions for tree regeneration, for example, by trapping litter and humus. This, in turn, can improve water and nutrient status, supporting seedling germination and survival (Yirdaw et al. 2015; Yirdaw et al. 2019). This may also explain higher soil moisture values found in the topsoils of the FAe and CDc communities as compared to SCt and SCb. In addition, litter and humus accumulation may generally improve seed storage, preventing rapid erosion.

Competition between tree regeneration and non-tree species in the SCt and SCb communities may also have resulted from former canopy disturbances. Increased light levels induce understorey growth with potential negative effects on tree regeneration. The light-demanding weed species Chloris barbata, identified as an indicator species in the SCb community, may be an indication of former disturbances as are the higher values of human impact indicators in SCt and SCb. However, the light availability measured for this study was around 9.17% ± 6.4% (mean ± sd) and homogeneous across communities.

Limitations of the study

Although we have considered many environmental factors and indicators of human impact to explain plant species composition and diversity in the CBNP, we acknowledge some shortcomings. We did not explicitly consider climatic factors (Slik et al. 2003; Cicuzza et al. 2013), such as rainfall and temperature. However, since sites were close to one another (compare Fig. 1), we did not expect great differences in climatic conditions. We also do not have detailed information on the disturbance history of the CBNP, even though evolutionary or historical disturbance processes may control the distribution of certain species in certain sites (Trejo and Dirzo 2002; Tuomisto et al. 2003; Chytrý et al. 2010). Finally, factors such as geographical distance or tectonics may also have played a role in the observed patterns of plant species composition and diversity; both of these factors might affect environmental conditions, habitat formation and floral assemblages (van Andel 2001; Slik et al. 2003; Júnior et al. 2014). In future research, it may also be worth focusing on plant functional groups, which would require more research into the autecology of the different tree and non-tree species.


Our study demonstrates that plant species composition and diversity in the CBNP vary strongly at the regional scale. Contrary to our expectations, the isolated island site did not contribute much to total plant species richness. Species found there seemed well adapted to the harsh conditions, but were also found at other sites and can, therefore, be classified as generalists.

We also showed that environmental factors are important drivers of plant species composition and species diversity in the CBNP with non-tree species contributing about 50% to total species richness. Our data indicate that this species group is less prone than tree species to environmental filtering. Furthermore, the coverage of non-tree species negatively impacted species richness of tree regeneration on sites with sufficient water and nutrient availability (Sterculia lanceolata + Chloris barbata and Saraca dives + Calamus tetradactylus community). Under harsh environmental conditions, non-tree species appeared to facilitate tree regeneration richness of the Ficus superba + Acanthus ebracteatus community, underscoring the important function of non-tree species to forest development in these tropical forests on limestone. The Sterculia lanceolata + Chloris barbata and the Saraca dives + Calamus tetradactylus community, found mainly in lowlands in transition to mid-slope conditions, contribute most to plant species diversity in the CBNP.

From these findings, we conclude that plant species composition and diversity in the CBNP is rich, with tree and non-tree species contributing equally to this diversity, but with higher tree species diversity in the lowlands. For future conservation management, the protection of tree species, for example, from illegal logging activities, should be one priority for managers of the CBNP. This is particularly important as the area most accessible to the local population is characterised by tree species-rich forest communities. In general, the main island contributes most to plant species richness in the CNBP due to the availability of microsites and connectivity amongst habitats. Thus, monitoring of species diversity and composition and conservation management to prevent fragmentation should focus on these areas. Here and beyond the CBNP, the dynamics of the identified indicator species groups will help to detect future changes in environmental conditions.

The identified forest communities with their indicator species assemblages provide fundamental information on the interactions between plant species distribution and environmental conditions in limestone forests of Vietnam and may also help to characterise the limestone forests beyond the borders of the CBNP.


This study was supported by the Vietnamese Government Scholarship (decision No.911), the Rufford Small Grants Foundation and the Georg-August Universität Göttingen, Silviculture and Forest Ecology of the Temperate Zones. The Open Access Publication Funds of the Georg-August-University Göttingen support open access publication. We are grateful to the directors of the Cat Ba National Park for their steady support during the fieldwork. In particular, we want to thank Hoang Van Thap, Doan Ngoc Son, Hoang Van Cau, Nguyen Van Khu, Nguyen Van Luc, Nguyen Van Thiep and Nguyen Van Tu for their fieldwork assistance. Thanks go also to Pham Ba Su and Doan Ngoc Son, who helped with tree identification; and to Tran Thi Hang, who helped with analysing the soil samples. We are grateful for linguistic corrections by Kathleen Regan (USA).


  • Assefa A, Demissew S, Woldu Z (2013) Floristic composition, structure and regeneration status of Masha forest, south-west Ethiopia. African Journal of Ecology 52(2): 151–162.
  • Bailey D, Schmidt-Entling MH, Eberhart P, Herrmann JD, Hofer G, Kormann U, Herzog F (2010) Effects of habitat amount and isolation on biodiversity in fragmented traditional orchards. Journal of Applied Ecology 47(5): 1003–1013.
  • Behera SK, Misra MK (2005) Floristic and Structure of the Herbaceous Vegetation of Four Recovering Forest Stands in the Eastern Ghats of India. Biodiversity and Conservation 15(7): 2263–2285.
  • Blanc L, Maury-Lechon G, Pascal JP (2000) Structure, floristic composition and natural regeneration in the forests of Cat Tien National Park, Vietnam: An analysis of the successional trends. Journal of Biogeography 27(1): 141–157.
  • Both S, Fang T, Bohnke M, Bruelheide H, Geissler C, Kuhn P, Scholten T, Trogisch S, Erfmeier A (2011) Lack of tree layer control on herb layer characteristics in a subtropical forest, China. Journal of Vegetation Science 22(6): 1120–1131.
  • Carle J, Holmgren P (2003) Definitions related to planted forests FAO, 16 pp.
  • CBNP (2005) Inventory and Planning for Cat Ba National Park from 2006 to 2010 and vision to 2020. Cat Ba National Park, Haiphong, Vietnam, 123 pp.
  • CBNP (2007) Biodiversity Information of Cat Ba National Park, Vietnam. Institute of Ecology and Resources, Cat Ba Nation Park, Haiphong, Vietnam, 203 pp.
  • Chao A, Jost L (2012) Coverage-based rarefaction and extrapolation: Standardizing samples by completeness rather than size. Ecology 93(12): 2533–2547.
  • Chao A, Gotelli NJ, Hsieh TC, Sander EL, Ma KH, Colwell RK, Ellison AM (2014) Rarefaction and extrapolation with Hill numbers: A framework for sampling and estimation in species diversity studies. Ecological Monographs 84(1): 45–67.
  • Chazdon RL (2003) Tropical forest recovery: Legacies of human impact and natural disturbances. Perspectives in Plant Ecology, Evolution and Systematics 6(1–2): 51–71.
  • Chytrý M, Danihelka J, Axmanová I, Božková J, Hettenbergerová E, Li C-F, Rozbrojová Z, Sekulová L, Tichý L, Vymazalová M, Zelený D (2010) Floristic diversity of an eastern Mediterranean dwarf shrubland: The importance of soil pH. Journal of Vegetation Science 21(6): 1125–1137.
  • Cicuzza D, Kromer T, Poulsen AD, Abrahamczyk S, Delhotal T, Piedra HM, Kessler M (2013) A transcontinental comparison of the diversity and composition of tropical forest understory herb assemblages. Biodiversity and Conservation 22(3): 755–772.
  • Cutler DR, Edwards Jr TC, Beard KH, Cutler A, Hess KT, Gibson J, Lawler JJ (2007) Random forests for classification in ecology. Ecology 88(11): 2783–2792.
  • Dao T, Hölscher D (2018) Impact of Non-Timber Forest Product Use on the Tree Community in North-Western Vietnam. Forests 9(7): e431. [1–15]
  • De Cáceres M, Legendre P (2009) Associations between species and groups of sites: indices and statistical inference. Ecology 90(12): 3566–3574.
  • Do HTT, Grant JC, Trinh BN, Zimmer HC, Nichols JD (2017) Diversity depends on scale in the forests of the Central Highlands of Vietnam. Journal of Asia-Pacific Biodiversity 10(4): 472–488.
  • EI-Bana MI (2009) Factors Affecting the Floristic Diversity and Nestedness in the Islets of Lake Bardawil, North Sinai, Egypt: Implications for Conservation. Journal of Coastal Conservation 13: 25–37.
  • Fang ZQ, Bao WK, Yan XL, Liu X (2014) Understory structure and vascular plant diversity in naturally regenerated deciduous forests and spruce plantations on similar clear-cuts: Implications for forest regeneration strategy selection. Forests 5(4): 715–743.
  • Fangliang H, Legendre P, Frankie JVL (1997) Distribution patterns of tree species in a Malaysian tropical rain forest. Vegetation Science 8(1): 105–114.
  • FSIV (2009) Vietnam Forestry outlook study. Food and agriculture organization of the united nations regional office for Asia and the Pacific. Bangkok, Thailand, 72 pp.
  • Galeano G, Suarez S, Balslev H (1998) Vascular plant species count in a wet forest in the Chocó area on the Pacific coast of Colombia. Biodiversity and Conservation 7(12): 1563–1575.
  • Gentry AH, Dodson C (1987) Contribution of nontrees to species richness of a tropical rain forest. Biotropica 19(2): 149–156.
  • Guo YL, Wang B, Mallik AU, Huang FZ, Xiang WS, Ding T, Wen SJ, Lu SH, Li DX, He YL, Li XK (2017) Topographic species-habitat associations of tree species in a heterogeneous tropical karst seasonal rain forest, China. Journal of Plant Ecology 10(3): 450–460.
  • Hill JL, Curran PJ (2003) Area, shape and isolation of tropical forest fragments: Effects on tree species diversity and implications for conservation. Journal of Biogeography 30(9): 1391–1403.
  • Holm LG, Pancho JV, Herberger JP, Plucknett DL (1979) A Geographical Atlas of World Weeds. John Wiley and Sons, New York, NY, USA.
  • Hothorn T, Bretz F, Westfall P (2008) Simultaneous inference in general parametric models. Biometrical Journal. Biometrische Zeitschrift 50(3): 346–363.
  • Hsieh TC, Ma KH, Chao A, McInerny G (2016) iNEXT: An R package for rarefaction and extrapolation of species diversity (Hill numbers). Methods in Ecology and Evolution 7(12): 1451–1456.
  • Júnior JAP, Lopes SF, Vale VS, Arantes CS, Oliveira AP, Schiavini I (2014) Floristic patterns in understoreys under different disturbance severities in seasonal forests. Journal of Tropical Forest Science 26: 458–468.
  • Kleinn C, Yihlam T, Yang H, Netra Schnell SB, Fehrmann L (2009) Forest Inventory. Goerg August Universität Göttingen, 189 pp.
  • Le MT (2006) Flora in Cat Ba National Park. Forest Inventory and Planning Institute, Hanoi, Vietnam, 17 pp.
  • Lillo EP, Fernando ES, Lillo MJR (2019) Plant diversity and structure of forest habitat types on Dinagat Island, Philippines. Journal of Asia-Pacific Biodiversity 12(1): 83–105.
  • Linares-Palomino R, Cardona V, Hennig EI, Hensen I, Hoffmann D, Lendzion J, Soto D, Herzog SK, Kessler M (2009) Non-woody life-form contribution to vascular plant species richness in a tropical American forest. Plant Ecology 201(1): 87–99.
  • MacArthur RH, Wilson EO (1967) The theory of island biogeography. Princeton University Press, Princeton, 203 pp.
  • MARD (2006) Lâm sản ngoài gỗ. CẨM NANG NGÀNH LÂM NGHIÊP, Bộ Nông nghiệp và Phát triển Nông thôn, Hà Nội, Việt Nam, 176 pp.
  • Martin-Queller E, Albert CH, Dumas PJ, Saatkamp A (2017) Islands, mainland, and terrestrial fragments: How isolation shapes plant diversity. Ecology and Evolution 7(17): 6904–6917.
  • Mendes G, Arroyo-Rodriguez V, Almeida WR, Pinto SRR, Pillar VD, Tabarelli M (2016) Plant trait distribution and the spatial reorganization of tree assemblages in a fragmented tropical forest landscape. Plant Ecology 217(1): 31–42.
  • Mezaka A, Bader MY, Allen NS, Mendieta-Leiva G (2020) Epiphyll specialization for leaf and forest successional stages in a tropical lowland rainforest. Journal of Vegetation Science 31(1): 118–128.
  • Nuttle T, Royo AA, Adams MB, Carson WP (2013) Historic disturbance regimes promote tree diversity only under low browsing regimes in eastern deciduous forest. Ecological Monographs 83(1): 3–17.
  • Pham VV, Ammer C, Annighöfer P (2020) The Presence of IUCN Red List Tree Species in Dependence of Site Characteristics in the Vietnamese Cat Ba National Park. Diversity (Basel) 12(3): e104. [1–17]
  • Pham VV, Ammer C, Annighöfer P, Heinrichs S (2022) Tree regeneration characteristics in limestone forests of the Cat Ba National Park, Vietnam. BMC Ecology and Evolution 22(1): e6.
  • Prieto PV, Sansevero JBB, Garbin ML, Braga JMA, Rodrigues PJFP (2014) Edge effects of linear canopy openings on understorey communities in a lowland Atlantic tropical forest. Applied Vegetation Science 17(1): 121–128.
  • Quinn JF, Harrison SP (1988) Effects of Habitat Fragmentation and Isolation on Species Richness: Evidence from Biogeographic Patterns. Oecologia 75(1): 132–140.
  • R Core Team R (2017) R: A language and environment for statistical computing. [accessed Septemper 28. 2017]
  • Santo‐Silva EE, Benchimol M, Peres CA, Schmidtlein S (2021) Phylogenetic homogenization of Amazonian tree assemblages in forest islands after 26 years of isolation. Applied Vegetation Science 24(3): e12601.
  • Scheffer M, van Geest GJ, Zimmer K, Jeppesen E, Søndergaard M, Butler MG, Hanson MA, Declerck S, De Meester L (2006) Small Habitat Size and Isolation Can Promote Species Richness: Second-Order Effects on Biodiversity in Shallow Lakes and Ponds. Oikos 112(1): 227–231.
  • Seta T, Demissew S, Woldu Z (2018) Floristic diversity and composition of the Biteyu forest in the Gurage mountain chain (Ethiopia): Implications for forest conservation. Journal of Forestry Research 30(1): 319–335.
  • Slik JWF, Poulsen AD, Ashton PS, Cannon CH, Eichhorn KAO, Kartawinata K, Lanniari I, Nagamasu H, Nakagawa M, Van Nieuwstadt MGL, Payne J, Saridan A, Sidiyasa K, Verburg RW, Webb CO, Wilkie P (2003) A Floristic Analysis of the Lowland Dipterocarp Forests of Borneo. Journal of Biogeography 30(10): 1517–1531.
  • Sodhi NS, Posa MRC, Lee TM, Bickford D, Koh LP, Brook BW (2009) The state and conservation of Southeast Asian biodiversity. Biodiversity and Conservation 19(2): 317–328.
  • Sorrenti S (2017) Non-wood forest products in international statistical systems. Non-wood Forest Products Series. FAO, Rome, 130 pp.
  • Sun BL, Zhang CQ, Lowry PP II, Wen J (2009) Cryptic Dioecy in Nyssa yunnanensis (Nyssaceae), a Critically Endangered Species from Tropical Eastern Asia. Annals of the Missouri Botanical Garden 96(4): 672–684.
  • Tardella FM, Postiglione N, Vitanzi A, Catorci A (2017) The effects of environmental features and overstory composition on the understory species assemblage in sub-Mediterranean coppiced woods: Implications for a sustainable forest management. Polish Journal of Ecology 65(2): 167–182.
  • Tateno R, Takeda H (2003) Forest structure and tree species distribution in relation to topography-mediated heterogeneity of soil nitrogen and light at the forest floor. Ecological Research 18(5): 559–571.
  • Thrippleton T, Bugmann H, Folini M, Snell RS (2018) Overstorey-Understorey Interactions Intensify After Drought-Induced Forest Die-Off: Long-Term Effects for Forest Structure and Composition. Ecosystems 21(4): 723–739.
  • Trichon V (1997) Spatial heterogeneity of a tropical rain forest in Sumatra: Effect of topography on floristic structure. Annales des Sciences Forestieres 54: 431–446.
  • Tsai HC, Chiang JM, McEwan RW, Lin TC (2018) Decadal effects of thinning on understory light environments and plant community structure in a subtropical forest. Ecosphere 9(10): e02464.
  • Tuomisto H, Ruokolainen K, Yli-Halla M (2003) Dispersal, Environment, and Floristic Variation of Western Amazonian Forests. Science 299(5604): 241–244.
  • Uhl B, Wölfling M, Fiedler K (2021) Local, forest stand and landscape-scale correlates of plant communities in isolated coastal forest reserves. Plant Biosystems - An International Journal Dealing with all Aspects of Plant Biology 155: 457–469.
  • van Andel T (2001) Floristic composition and diversity of mixed primary and secondary forests in northwest Guyana. Biodiversity and Conservation 10(10): 1645–1682.
  • Vivian-Smith G (1997) Microtopographic Heterogeneity and Floristic Diversity in Experimental Wetland Communities. Journal of Ecology 85(1): 71–82.
  • Wester L (1992) Origin and distribution of adventive alien flowering plants in Hawaii. In: Stone CP, Smith CW, Tunison JT (Eds) Alien plant invasions in native ecosystems of Hawaii: management and research. University of Hawaii Press, Honolulu, Hawaii, USA, 99–154.
  • Yavitt JB, Harms KE, Garcia MN, Wright SJ, He F, Mirabello MJ (2009) Spatial heterogeneity of soil chemical properties in a lowland tropical moist forest, Panama. Australian Journal of Soil Research 47(7): 674–687.
  • Yirdaw E, Starr M, Negash M, Yimer F (2015) Influence of topographic aspect on floristic diversity, structure and treeline of afromontane cloud forests in the Bale Mountains, Ethiopia. Journal of Forestry Research 26(4): 919–931.
  • Yirdaw E, Monge AM, Austin D, Toure I (2019) Recovery of floristic diversity, composition and structure of regrowth forests on fallow lands: Implications for conservation and restoration of degraded forest lands in Laos. New Forests 50(6): 1007–1026.
  • Zhang CS, Xie GD, Fan SH, Zhen L (2010) Variation in Vegetation Structure and Soil Properties, and the Relation Between Understory Plants and Environmental Variables Under Different Phyllostachys pubescens Forests in Southeastern China. Environmental Management 45(4): 779–792.
  • Zhang QW, Zhu SD, Jansen S, Cao KF (2021) Topography strongly affects drought stress and xylem embolism resistance in woody plants from a karst forest in Southwest China. Functional Ecology 35(3): 566–577.
  • Zhu SD, Li RH, Song J, He PC, Liu H, Berninger F, Ye Q (2016) Different leaf cost-benefit strategies of ferns distributed in contrasting light habitats of sub-tropical forests. Annals of Botany 117(3): 497–506.

Appendix 1

Figure A1.

Communities’ dendrogram in Cat Ba National Park. The numbers 1, 2, 3 and 4 showed the order of forestry communities after hierarchical cluster analysis. 1, Saraca dives + Calamus tetradactylus community (SCt); 2, Sterculia lanceolata + Chloris barbata community (SCb); 3, Ficus superba + Acanthus ebracteatus community (FAae); 4, Clausena excavata + Desmos cochinchinensis community (CDc). The “Height” axis shows the clustering height value associated with the Ward clustering method. The text of each branch showed the acronym of sample plots. LLA, low land area; MSA, mid-slope area; ISA, isolated area.

Appendix 2

Table A1.

The information of representative species of the four communities. If not stated otherwise, photographs were taken by Van Vien Pham.

Species information Image
Species: Saraca dives
Family: Fabaceae
Character: Small timber, tree height around 7–8 m. This species distributes near the stream, canals, water sources or humid areas, thick forests; distributed from north to central Vietnam.
Species: Calamus tetradactylus
Family: Arecaceae
Character: Vines, It grows in evergreen forest and scrub between 1 and 1000 m elevation and in Delta areas. This species has valuable in craft making and trade in Vietnam.
Species: Sterculia lanceolata
Family: Sterculiaceae
Character: Small timber tree, this species grows in mountainous areas, especially the hillsides in the midlands. The tree has large green leaves all year round and is suitable for moist areas. Flowers look like a star shape and in red. Distributed from Nnorth to central Vietnam.
Species: Chloris barbata
Family: Poaceae
Character: Annual grass; distribution in dry places, especially coastal areas.
Species: Ficus superba
Family: Moraceae
Character: This species is a small to medium timber tree species, tree height is from 5–15 m. It grows favourably in rich nutrient soil, with good moisture and drainage, is also a drought-tolerant species, not fussy about cultivated soil. This species has a very strong regeneration. Its distribution is throughout Vietnam.
Species: Acanthus ebracteatus
Family: Acanthaceae
Character: Shrub trees with a height from 1–3 m. This species has a wide distribution; can be found in many habitats, such as in dense and open forests, coastal, valleys and swampy areas, water banks, estuarine areas and moist forests.
Species: Clausena excavata
Family: Rutaceae
Character: Small timber tree. Tree height is around 5–6 m. It distributes from north to Ccentral Vietnam.
Species: Desmos cochinchinensis
Family: Annonaceae
Character: Climber, branches whitish or rusty-red hairy, petals hairy, fruits red. It grows in stunted, poor forests.

Appendix 3

Table A2.

The environmental and human activity characteristics in the three study sites (LLA, MSA and ISA) in Cat Ba National Park. The values represent the mean and standard deviation of 30 plots per study site (in total 90 plots). Small letters indicate significant differences at p ≤ 0.05 between the three areas. The “multicomp” package was used to calculate differences between the three study sites (Hothorn et al. 2008). The acronym column shows the abbreviation of the factor. T, terrain factors; S, soil properties; L, light availabilities; and H, human disturbances.

Factors Acronym Average LLA MSA ISA
Slope (°) T_Sl 17.23 ± 10.71 13.70 ± 9.67a 19.02 ± 10.38b 21.85 ± 10.62c
Rock surface (%) T_RS 44.49 ± 31.62 22.71 ± 23.02a 56.71 ± 22.84b 71.99 ± 23.07c
Elevation (m) T_Ele 75.33 ± 38.92 78.06 ± 37.02b 66.57 ± 37.40a 78.35 ± 42.30b
Soil depth (cm) S_SD 61.78 ± 38.77 75.89 ± 40.24b 51.97 ± 31.25a 45.67 ± 32.84a
Rock in soil (%) S_SR 9.59 ± 15.95 11.31 ± 19.83b 10.75 ± 14.96b 5.50 ± 3.77a
Soil moisture (%) S_SM 8.98 ± 5.72 5.98 ± 5.26a 11.06 ± 4.40b 12.41 ± 4.72c
Sand (%) S_Sand 31.45 ± 12.86 32.40 ± 11.26b 24.75 ± 7.35a 35.76 ± 16.55c
Silt (%) S_Silt 40.10 ± 8.18 41.95 ± 7.35b 41.73 ± 5.48b 35.37 ± 9.62a
Clay (%) S_Clay 28.45 ± 9.48 25.64 ± 10.47a 33.52 ± 5.25c 28.86 ± 8.61b
Soil humus content (%) S_SH 3.11 ± 1.49 2.67 ± 1.32a 2.76 ± 1.24a 4.20 ± 1.44b
pH S_pH 5.10 ± 0.56 4.79 ± 0.50a 5.40 ± 0.53b 5.39 ± 0.36b
Hydrolytic acidity (mmol /100 g) S_HA 5.01 ± 2.11 5.12 ± 1.98b 4.58 ± 1.97a 5.20 ± 2.38b
Cation exchange capacity (mmol / 100 g) S_CEC 6.92 ± 1.53 6.12 ± 1.43a 7.33 ± 1.11b 7.96 ± 1.22c
Base saturation (%) S_BS 58.88 ± 11.66 55.34 ± 12.09a 62.78 ± 11.11b 61.64 ± 9.31b
Indirect site factor L_ISF 9.17 ± 6.40 8.21 ± 2.75a 10.37 ± 11.68b 9.81 ± 3.39b
Footpaths H_FP 1.19 ± 0.45 1.25 ± 0.43b 1.17 ± 0.57a 1.11 ± 0.31a
Stumps H_STP 0.11 ± 0.31 0.21 ± 0.41b 0.02 ± 0.15a 0.00 ± 0.00a
Animal traps H_AT 0.65 ± 1.42 0.54 ± 1.16a 0.33 ± 2.03b 1.22 ± 0.95a

Appendix 4

Figure A2.

Classification tree of abiotic factors differentiating amongst communities. The regression tree shows independent environmental factors most closely related to the variation of communities. The communities were shown at the bottom of each branch of the independent environmental factors. The graph classifies environmental factors according to predictive strength (top to bottom). Abbreviations of the abiotic factors are defined in Table 3 and Appendix 3. The numbers give the communities: 1 = Saraca dives + Calamus tetradactylus community. 2 = Sterculia lanceolata + Chloris barbata community. 3 = Ficus superba + Acanthus ebracteatus community. 4 = Clausena excavata + Desmos cochinchinensis community.

Appendix 5

Table A3.

Estimated species pool of the CBNP. The estimation was based on all communities and for different combinations of communities. The value in the brackets represents the lower and upper confidence interval at 95%. SCt; Saraca dives + Calamus tetradactylus community. SCb; Sterculia lanceolata + Chloris barbata community. FAe; Ficus superba + Acanthus ebracteatus community. CDc; Clausena excavata + Desmos cochinchinensis community. The highest and lowest estimated values for the different community combinations are written in bold.

Species richness Shannon diversity Simpson diversity
(q = 0) (q = 1) (q = 2)
Estimated species pool for all communities (SCt+SCb+FAe+CDc) 367.7 159.8 105.4
(339.3 ÷ 417.7) (154.4 ÷ 165.2) (102.9 ÷ 108.9)
Combination of communities:
SCb+FAe+CDc 358.4 149 97
(318.1 ÷ 429.6) (142.6 ÷ 155.5) (94.2 ÷ 100.8)
SCt+FAe+CDc 334.7 147.9 97.5
(300.8 ÷ 394.4) (141 ÷ 154.8) (94.2 ÷ 102.1)
SCt+SCb+CDc 354.7 160.1 106.4
(324.4 ÷ 408.5) (154.1 ÷ 166) (103.4 ÷ 110.8)
SCt+SCb+FAe 377.9 166.6 109.7
(343.1 ÷ 437.9) (160.6 ÷ 172.6) (106.3 ÷ 114.3)
FAe+CDc 244.3 106.8 71.4
(209.3 ÷ 313.2) (100.8 ÷ 112.8) (68.8 ÷ 75.3)
SCb+CDc 338.6 151.1 99.9
(296.9 ÷ 413.9) (143.7 ÷ 158.5) (96.2 ÷ 104.5)
SCb+FAe 357.1 160.7 104.7
(313.6 ÷ 433.2) (153.4 ÷ 168.1) (100.3 ÷ 109.6)
SCt+CDc 328 147.9 97.7
(283.9 ÷ 407.5) (139.68 ÷ 156.2) (93.2 ÷ 102.7)
SCt+FAe 327.5 158 104.6
(289.4 ÷ 394.3) (149.3 ÷ 166.7) (99.16 ÷ 110)
SCt+SCb 356.4 161.5 106.8
(319.6 ÷ 420.2) (154.3 ÷ 168.7) (103 ÷ 111.6)

Appendix 6

Figure A3.

Species diversity patterns of the tree and non-tree species. The graphs show the Shannon (q = 1) and Simpson diversity (q = 2) (Hill number) from iNEXT analysis. The red colour represented the total tree species of all four communities (gamma diversity). Yellow-green colour represented the Saraca dives + Calamus tetradactylus community (SCt). The green colour represented the Sterculia lanceolata + Chloris barbata community (SCb). Light-blue represented Ficus superba + Acanthus ebracteatus community (FAe) and pink colour represented Clausena excavata + Desmos cochinchinensis community (CDc). The fade of the line showed the confidence level at 95%.

Appendix 7

Figure A4.

Linear models of non-tree species and threatened tree species abundance. Graphs (a) and (c) show the relationship between non-tree species and threatened tree species abundance across communities. Graphs (b) and (d) present the relationship of non-tree species to threatened tree species abundance separated by the four communities. All relationships are not significant as indicated by the dashed lines. SCt; Saraca dives + Calamus tetradactylus community. SCb; Sterculia lanceolata + Chloris barbata community. FAe; Ficus superba + Acanthus ebracteatus community. CDc; Clausena excavata + Desmos cochinchinensis community.

Appendix 8

Table A4.

Species checklist. This table contains the 302 species which were recorded in the CBNP in course of this study. It includes 153 tree species (comprising the overstorey layer and the regeneration layer) and 149 non-tree species. The classification is provided as well.

No Species name Family Indigenous name Classification
1 Acacia lucium (Benth). I: Nielsen Mimosaceae Mán đỉa trâu Tree
2 Acanthus ebracteatus Vahl. Acanthaceae Ô rô Non-tree
3 Achyranthes aspera L. Amaranthaceae Cỏ xước Non-tree
4 Acronychia pedunculata L. Rutaceae Bưởi bung Tree
5 Actinodaphne pilosa (Lour.) Merr. Lauraceae Tam tầng Non-tree
6 Adenanthera pavonica L. Mimosaceae Muồng ràng ràng Tree
7 Aesculus assamica Griff. Hippocastanaceae Kẹn Non-tree
8 Aglaia poilanei Pell. Meliaceae Ngâu dại Non-tree
9 Aglaia spectabilis (Miq.) Jain& Bennet. 1987 Meliaceae Gội nếp Tree
10 Aidia pycnantha (Drake) Tirveng Rubiaceae Mãi táp Tree
11 Albizia chinensis (Osbeek) Merr Fabaceae Đuôi trâu Tree
12 Allophylus livescens Radlk. Sapindaceae Vải đóm Non-tree
13 Allospondias lakonensis (Pierre) Stapf Anacardiaceae Dâu da xoan Tree
14 Alpinia officinarum Hance Zingiberaceae Riềng ré Non-tree
15 Alstonia scholaris (L.) R.Br. Apocynaceae Sữa Tree
16 Amomum xanthioides Wall. ex Baker Zingiberaceae Sa nhân núi Non-tree
17 Amorphophalus tonkinensis Engl. & Gehrm. Araceae Nưa bắc bộ Non-tree
18 Angiopteris evecta (J.R. Forst.) Hoffm. Angiopteridaceae Quan âm tọa liên Non-tree
19 Annamocarya sinensis (Dode) J. Leroy Juglandaceae Chò đãi Tree
20 Annona glabra L. Annonaceae Na biển Tree
21 Antidesma ambiguum Pax et Hoffm. Euphorbiaceae Chòi mòi Non-tree
22 Aphanamixis polystachya (Wall.) R. Parke Meliaceae Gội gác Tree
23 Aporosa macrostachyus (Tul.) Muell.Arg. Euphorbiaceae Tai nghé đuôi to Tree
24 Aporusa ficifolia H. Baillon Euphorbiaceae Tai nghé Tree
25 Aralia aff. chinensis L. Araliaceae Quầng quầng Non-tree
26 Archidendron clypearia Fabaceae Mán đỉa Tree
27 Ardisia crenata Sims Primulaceae Trọng đũa Non-tree
28 Ardisia gigantifolia Stapf Primulaceae Lá khôi trắng Non-tree
29 Ardisia nigropilosa Pit. Primulaceae Trọng đũa lông đen Non-tree
30 Ardisia silvestris Pitard. Myrsinaceae Lá khôi tía Non-tree
31 Arenga westerhoutii Griffith Arecaceae Búng báng Non-tree
32 Artocarpus borneensis Merr. Subsp. Griffthii (Kurz) Jarr. Moraceae Troi Tree
33 Asplenium nidus (L.) J.Sm. Aspleniaceae Tổ điểu Non-tree
34 Atalantia guillauminii Sw. Rutaceae Quýt hôi Tree
35 Averrhea carambola L. Oxalidaceae Khế Tree
36 Bambusa blumeana J. A. & J. H. Schultes Poaceae Tre gai Non-tree
37 Bambusa chungii McClure Poaceae Dùng phấn Non-tree
38 Barringtonia acutangula (L.) Gaertn. Lecythidaceae Lộc vừng lá to Tree
39 Bauhinia coccinea (Lour.) A. DC. Caesalpiniaceae Móng bò hoa đỏ Non-tree
40 Bauhinia khasiana var. polystachya (Gagnep.) K.&S.S.Larsen Caesalpiniaceae Dây quạch tròn Non-tree
41 Bauhinia lakhonensis Gagnep Caesalpiniaceae Dây quạch dẹt Non-tree
42 Bauhinia ornata Kurz Caesalpiniaceae Dây móng bò thơm Non-tree
43 Begonia aff. wallichinia A. DC. Begoniaceae Thu hải đường vát Non-tree
44 Bischofia javanica Blume (B. trifoliata (Roxb.) Hook. f.) Euphorbiaceae Nhội tiết Tree
45 Blechnum orientale L. Blechnaceae Quyết lá dừa Non-tree
46 Blumea lacineata (Roxb.) DC. Asteraceae Dẻ rách Non-tree
47 Boehmeria holoseracea Blume Urticaceae Gai rừng Non-tree
48 Boehmeria nivea (L) Gaud Urticaceae Lá gai Non-tree
49 Bombax malabarica DC. Bombacaceae Gạo rừng Tree
50 Breynia fruticosa (L.) Hook. f. Euphorbiaceae Bồ cu vẽ Non-tree
51 Bridelia balansae Tutcher Euphorbiaceae Đỏm gai Tree
52 Bridelia tomntosa Blume Euphorbiaceae Đỏm lông Tree
53 Burretiodendron brilletii (Gagn.) Kost. Tiliaceae Kiêng quang Tree
54 Bursera tonkinensis Guillaum Burseraceae Rẫm Tree
55 Caesalpinia bonduc (L.) Roxb. Caesalpiniaceae Dây móc mèo Non-tree
56 Calamus platyacanthus Warb. Ex Becc. Arecaceae Song mật Non-tree
57 Calamus tetradactylus Hance Arecaceae Mây Non-tree
58 Callicarpa triloba Lour. Vitaceae Chìa vôi Non-tree
59 Canarium album Burseraceae Trám trắng Tree
60 Canarium subulatum Guill Burseraceae Trám ba cạnh Tree
61 Canarium tramdenum Dai &Yakovl Burseraceae Trám đen Tree
62 Canthium dicoccum (Gaertn.) Teysm. & Binn Rubiaceae Xương cá Tree
63 Carallia brachiata (Lour.) Merr. Rhizophoraceae Trúc tiết Tree
64 Carallia diplopetala Rhizophoraceae Răng cá Tree
65 Caryota obtusa Griff. Arecaceae Đùng đình Non-tree
66 Caryota urens L. Palmeae Móc Non-tree
67 Cassia timoriensis A. DC. Caesalpiniaceae Muồng cánh dán Tree
68 Castanopsis chinensis (Spreng.) Hance. Fagaceae Dẻ gai Tree
69 Castanopsis ferox (Roxb.) Spach Fagaceae Cà ổi vọng phu Tree
70 Celastrus hindsii Benth. & Hook. Celastraceae Xạ vàng Non-tree
71 Celastrus sp. Celastraceae Xạ đen Non-tree
72 Centella asiatica (L.) Urb. Apiaceae Ráu má Non-tree
73 Chisocheton paniculatus Hiern Meliaceae Quếch tía Tree
74 Chloris barbata Sw. Poaceae Cỏ mật Non-tree
75 Chromolaena odorata (L.) King et Robinson Asteraceae Cỏ lào Non-tree
76 Chukrasia tabularis A. Juss. Meliaceae Lát hoa Tree
77 Cinnamomum ovantum Allen. Lauraceae Rè gừng Tree
78 Cissus subtetragona Blume Vitaceae Hồ đằng vuông Non-tree
79 Citrus aurantiifolia (Chritm.) Sw. Rutaceae Chanh rừng Non-tree
80 Claoxylon indicum (Reinw.ex Blume) Euphorbiaceae Lộc mại Tree
81 Clausena excavata Burm.f. Rutaceae Hồng bì rừng Tree
82 Cleistanthus myrianthus (Hassk.) Kurz Euphorbiaceae Cọc rào Non-tree
83 Clerodendrum chinense (Osk.) Mabb. Fagaceae Ngọc nữ thơm Non-tree
84 Clerodendrum squamatum Vahl Verbenaceae Xích đồng nam Non-tree
85 Cnestis palala (Lour.) Merr. Connaraceae Dây khế Non-tree
86 Colocaria gigantea (Blume ex Hassk) Hook.f. Araceae Ráy Non-tree
87 Commelina communis L. Commelinaceae Thài lài Non-tree
88 Connarus paniculatus Roxb. Connaraceae Dây mấu Non-tree
89 Convolvulus parviflorus Vohl. Convolvulaceae Bìm bìm Non-tree
90 Cordyline fruticosa (L.) Goepp. Asteliaceae Huyết dụ Non-tree
91 Cratoxylon formosum subsp.prunifolium (Kurz) Gog. Guttiferae Đỏ ngọn Tree
92 Cratoxylum cochinchinense (Lour.) Blume Hypericaceae Thành ngạnh Tree
93 Croton cubiensis Gagn. Euphorbiaceae Cù đèn Non-tree
94 Cryptocarya lenticellata Lecomte Lauraceae Nanh chuột Tree
95 Curculigo gracilis (Kurz) Wall. Hypoxidaceae Sâm cau Non-tree
96 Cyclosorus parasiticus (L.) Farw. Thelypteridaceae Dương xỉ Non-tree
97 Cymbidium hybrid Orchidaceae Địa lan Non-tree
98 Cymbodium alviclium sw. Orchidaceae Lan kiếm Non-tree
99 Desmos cochinchinensis Lour. Annonaceae Dây hoa dẻ Non-tree
100 Deutzianthus tonkinensis Gagnep Euphorbiaceae Mọ Tree
101 Dianella ensifolia (L.) DC. Phormiaceae Hương bài Non-tree
102 Dichroa febrifuga Lour. Hydrangeaceae Thường sơn Non-tree
103 Dillenia heterosepala Fin&Gagnep Dilleniaceae Lọng bàng Tree
104 Dillenia indica L. Dilleniaceae Sổ bà Tree
105 Dillenia scabrella Roxb Dilleniaceae Sổ nước Tree
106 Dimocarpus fumatus subsp. indochinensis Leenh Sapindaceae Nhãn rừng Tree
107 Dioscorea alata L Dioscoreaceae Củ mỡ Non-tree
108 Dioscorea persimilis Prain et Burk. Dioscoreaceae Củ mài Non-tree
109 Diospyros decandra Lour Ebenaceae Nhọ nồi Tree
110 Diospyros petelotii Merr. Ebenaceae Thị mấm Tree
111 Diospyros pilosula (A. DC.) Hiern Ebenaceae Thị rừng Tree
112 Diospyros susarticulata Lec, Ebenaceae Thị đốt cao Tree
113 Donella lanceolata (Bl.) Aubr. Sapotaceae Sạp đỏ Non-tree
114 Dracaena sanderiana forma virescens Hort. Dracaenaceae Sống đời Non-tree
115 Dracontomelon duperreanum Piere Anacardiaceae Sấu Tree
116 Drimycarpus racemosus Hook. Anacardiaceae Sơn xã Tree
117 Drynaria fortunei (Merr.) J.Sm. Polypodiaceae Bổ cốt toái Non-tree
118 Duabanga grandiflora (DC.) Walp. Sonneratiaceae Phay sừng Tree
119 Elaeagnus bonii Lecomte Elaeagnaceae Nhót rừng Non-tree
120 Elaeocarpus griffithii (Wight) A. Gray Elaeocarpaceae Côm tầng Tree
121 Elephantopus mollis H.B.K. Asteraceae Chân voi Non-tree
122 Eleusine indica (L.) Gaertn. Poaceae Cỏ mần trầu Non-tree
123 Embelia laeta (L.) Mez. Myrsinaceae Rè vũ Non-tree
124 Endospermum chinense Benth. Euphorbiaceae Vạng trứng Tree
125 Engelhardtia roxburghiana Wall Juglandaceae Chẹo tía Tree
126 Entada glandulosa Pierre ex Gagn. Mimosoideae Bàm bàm tuyến Non-tree
127 Eriobotrya bengalensis (Roxb.) Hook.f. Rosaceae Tỳ bà rừng Tree
128 Erythrophleum fordii Oliv. Caesalpiniaceae Lim xanh Tree
129 Euodia lepta (Spreng) Merr. Rutaceae Chè đắng Tree
130 Eurya ciliata Merr. Theaceae Súm lông Tree
131 Eurycoma longifolia Jack. Simaroubaceae Bền bệt Non-tree
132 Excoecaria cochinchinensis var. viridis (Pax & Hoffm.)Merr. Euphorbiaceae Sơn đề Non-tree
133 Ficus alongensis Gagnep Moraceae Sung hạ long Tree
134 Ficus altissima Blume Moraceae Đa trâu Tree
135 Ficus annulata Blume Moraceae Đa nhộng vàng Tree
136 Ficus auriculata Lour. Moraceae Vả Tree
137 Ficus capillipes Gagn. Moraceae Đa cuống bẹt Tree
138 Ficus chlorocarpa Benth. Moraceae Sung rừng Tree
139 Ficus hirta Vahl Moraceae Vú bò Non-tree
140 Ficus hispida L.f. Moraceae Ngái Tree
141 Ficus retusa L. Moraceae Si Tree
142 Ficus rumphii Bl. Moraceae Da bò Tree
143 Ficus superba var.japonica Miq. Moraceae Sộp Tree
144 Garcinia cochinchinesis (Lour.) Choisy Clusiaceae Bứa tai chua Tree
145 Garcinia cowa Roxb. ex DC. Clusiaceae Tai chua Tree
146 Garcinia oblongifolia Champ. Clusiaceae Bứa Tree
147 Garcinia tinctoria (DC.) W. Wight Clusiaceae Bứa cơm Tree
148 Garruga pinnata Roxb. Burseraceae Trám mao Tree
149 Gelsemium elegans Gelsemiaceae Dây lá ngón Non-tree
150 Gigantochloa albo-ciliata (Munro) Kurz Poaceae Le Non-tree
151 Gironniera subequalis Planch. Ulmaceae Ngát Tree
152 Gleichenia linearis Clarke Gleicheniaceae Ràng ràng Non-tree
153 Glochidion hirsutum (Roxb.) Voigt Euphorbiaceae Bọt ếch biển Tree
154 Glycosmis cymosa (Pierre) Stone Rutaceae Màu cau đá Tree
155 Gnetum montanum Gnetaceae Dây gắm Non-tree
156 Gomphandra tonkinensis Gapnep Icacinaceae Bổ béo Non-tree
157 Goniothalamus macrocalyx Ban Annonaceae Màu cau trắng Tree
158 Gynostemma pentaphyllum Cucurbitaceae Giảo cổ lam Non-tree
159 Helicteres angustifolia L. Sterculiaceae Tổ kén tròn Non-tree
160 Helicteres hirsuta Lour Malvaceae Thao kén cái Non-tree
161 Helixanthera parasitica Lour. Loranthaceae Tầm gửi ký sinh Non-tree
162 Heterosmilax gaudichaudiana (Kunth.) Maxim Smilacaceae Khúc khắc Non-tree
163 Hydnocarpus hainanensis (Merr.) Sleum. Flacourtiaceae Nang trứng hải nam Tree
164 Iodes cirrhosa Turez Icacinaceae Mộc thông Non-tree
165 Ixora umbellata Vahl Rubiaceae Đơn ớt Non-tree
166 Jasminum subtriplinerve Oleaceae Chè vằng Non-tree
167 Knenma conferta Warb. Myristicaceae Máu chó Tree
168 Lagerstroemia calyculata Kurz Lythraceae Săng lẻ Tree
169 Lemmaphyllum microphyllum Presl. Polypodiaceae Tắc kè đá Non-tree
170 Lilium brownii F.E Brown var colchesteri Wilson Liliaceae Tỏi rừng Non-tree
171 Liquidambar formosana Hance Hamamelidaceae Sau sau Tree
172 Lithocarpus fissus Champ. ex benth Fabaceae Sồi phảng Tree
173 Lithocarpus hemisphaericus (Drake) Barnett Fagaceae Trâm dày Tree
174 Litsea monopetala (Roxb.) Pers. Lauraceae Mò giấy Tree
175 Litsea verticillata Hance Lauraceae Bời lời vòng Tree
176 Livistona halongensis T.H. Nguyen & Kiew Arecaceae Cọ hạ long Tree
177 Lonicera japonica Thunb. Caprifoliaceae Kim ngân Non-tree
178 Lycopodiella cernua (L.) Franco & Vasc. Arecaceae Thông đất Non-tree
179 Lygodium japonicum Sw Lygodiaceae Bòng bong Non-tree
180 Macaranga denticulata (Blume) Muell. Arg. Euphorbiaceae Lá nến Tree
181 Machilus bonii Lecomte Lauraceae Kháo vàng Tree
182 Machilus salicina Hance Lauraceae Kháo lá liễu Tree
183 Machilus thunbergii Sieb. & Zucc. Lauraceae Rè thunberg Tree
184 Machilus velutina Champ. ex Benth. Lauraceae Kháo lông Tree
185 Maclura cochinchinensis (Lour.) Moraceae Mỏ quạ Non-tree
186 Maesa balansae Mez. Myrsinaceae Đơn nem Non-tree
187 Maesa montana A.DC. Myrsinaceae Đơn độc trắng Non-tree
188 Maesa ramentacea Wall. Myrsinaceae Đơn độc đỏ Non-tree
189 Magnolia balansae Magnoliaceae Giổi bà Tree
190 Malaisia scandens (Lour.) Pl. Moraceae Duối leo Non-tree
191 Mallotus apelta (Lour.) Muell.-Arg. Euphorbiaceae Ba bét trắng Non-tree
192 Mallotus cochinchinensis Lour. Euphorbiaceae Ba soi Tree
193 Mallotus philippensis (Lamk.) Muell.-Arg. Euphorbiaceae Cánh kiến Non-tree
194 Mangifera longipes Griff. Anacardiaceae Trôi Tree
195 Manglietia rufibarbata Dandy Magnoliaceae Giổi xanh Tree
196 Markhamia cauda-felina (Hance) Craib. Bignoniaceae Kè đuôi nhông Tree
197 Melaleuca cajuputi Powell Myrtaceae Tràm nước Tree
198 Melodinus annamensis Pit. Apocynaceae Dây rom sữa Non-tree
199 Memecylon edule Roxb. Melastomataceae Sầm sì Tree
200 Mesua ferrea L. Clusiaceae Vắp Tree
201 Microcos paniculata Miq Tiliaceae Mé cò ke Tree
202 Microsorum hancockii (Bak.) Ching. Polypodiaceae Lá han Non-tree
203 Millettia pulchra Kunz Fabaceae Nam bạch chỉ Non-tree
204 Millettia sp Papilionoideae Tree
205 Morinda citrifolia L.var.bracteata Hook.f. Rubiaceae Nhàu Tree
206 Murraya glabra (Guillaum.) Rutaceae Vương tùng Tree
207 Musa paradisiaca L. Musaceae Chuối rừng Non-tree
208 Mussaenda crosa Champ. ex Benth. Rubiaceae Bướm bạc môn Non-tree
209 Mussaenda pilosissima Val. Rubiaceae Dây bướm lông Non-tree
210 Nervilia fordii (Hance) Sch. Orchidaceae Lan một lá Non-tree
211 Paliorus tonkinensis Pit. Rhamnaceae Táo dáng Tree
212 Pandanus tectorius Sol ex Park. Pandanaceae Dứa dại Non-tree
213 Paramichelia baillonii (Pierre) Hu Magnoliaceae Giổi găng Tree
214 Pavetta indica L. Rubiaceae Cẳng gà Tree
215 Peltophorum pterocarpum Caesalpiniaceae Lim xẹt Tree
216 Persea balansae Airy-Shaw Lauraceae Kháo lá to Tree
217 Persea mollis (W.W.Sm.) Kost. Lauraceae Kháo tai trâu Tree
218 Pheobe tavoyana Meisn. Lauraceae Sụ lá to Tree
219 Phoebe pallida Nees. Lauraceae Kháo nước Tree
220 Phrynium placentarium (Lour.) Merr. Maranthaceae Lá dong Non-tree
221 Phyllanthus reticulatus Poir. Euphorbiaceae Phèn đen Non-tree
222 Phytele phantoideae Arecaceae Xuôi Non-tree
223 Piper chaudocanum C. DC Piperaceae Trầu rừng Non-tree
224 Piper lolot C. DC. Piperaceae Lá lốt Non-tree
225 Podocarpus fleuryi Hickel Podocarpaceae Kim giao Tree
226 Portulaca oleacea L. Portulacaceae Sam núi đá Non-tree
227 Psychotria montana Blume Rubiaceae Lấu Non-tree
228 Pteris vittata L. Pteridaceae Chân rết Non-tree
229 Pterospermum diversifolium Sterculiaceae Lòng mang lá đa dạng Tree
230 Pterospermum heterophyllum Hance Sterculiaceae Lòng mang xanh Tree
231 Pterospermum truncatolobatum Gagn. Sterculiaceae Lòng mang cụt Tree
232 Quercus platycalyx Hickel & A. Camus Fabaceae Sồi đĩa Tree
233 Quisqulis indica L. Combretaceae Dây dầu giun Non-tree
234 Randia dasycarpa (Kurz) Bakh. f Rubiaceae Găng nhung Non-tree
235 Rauvolfia cambodiana Pierre ex Pit. Apocynaceae Ba gạc Non-tree
236 Rauvolfia verticillata (Lour.) Baill. Apocynaceae Ba gạc vòng Non-tree
237 Rhapis micrantha Becc Arecaceae Lụi Non-tree
238 Rhizophora apiculata Bl. Rhizophoraceae Đước đôi Tree
239 Rhodoleia championii Hook. Hamamelidaceae Hồng quang Non-tree
240 Rhus chinensis Muell. Anacardiaceae Dâu dắt Tree
241 Rinorea bengalensis (Wall.) Kuntze Violaceae Ngát giả Tree
242 Sapium discolor (Champ. ex Benth.) Muell.-Arg. Euphorbiaceae Sòi tía Tree
243 Saraca dives Fabaceae Vàng anh Tree
244 Sargentodoxa cuneata (Oliv.) Rehd. et Wiis. Sargeniodoxceae Huyết đằng Non-tree
245 Sauropus androgynus (L.) Merr Euphorbiaceae Rau ngót rừng Non-tree
246 Sauropus macranthus Hassk. Euphorbiaceae Vỏ rộp Non-tree
247 Schefflera alongensis R.Vig. Araliaceae Chân chim hạ long Non-tree
248 Schefflera heptaphylla (L.) Frodin Araliaceae Chân chim tám lá Non-tree
249 Schizostachyum dulloa Poaceae Nứa tép Non-tree
250 Secamone elliptica R.Br. Asclepiadaceae Ro bầu dục Non-tree
251 Selaginella decipiens Warb. Selaginellaceae Quyển bá Non-tree
252 Selaginella delicatula (Desv.) Alst. Selaginellaceae Quyển bá mỏng Non-tree
253 Sindora tonkinensis A. Chev. ex K. S. Larsen Caesalpiniaceae Gụ lau Tree
254 Sinosideroxylon racemosum (Dub.) Aubr. Sapotaceae Mai lai Tree
255 Sloanea sp. Elaeocarpaceae Côm nhím Tree
256 sp. 1 Moraceae Đèo heo Tree
257 sp. 2 Euphorbiaceae Mấy Tree
258 sp. 3 Rubiaceae Đèn en Tree
259 sp. 4 sp4 Áng nước Tree
260 sp. 5 sp5 Vấp Tree
261 Spilanthes paniculata Wall. ex DC Asteraceae Cây cúc áo Non-tree
262 Sporobolus fertilis (Steud.) Calayton Poaceae Cỏ lông công Non-tree
263 Stephania rotunda Lour. Menispermaceae Bình vôi Non-tree
264 Sterculia foetida L. Sterculiaceae Mần lái Tree
265 Sterculia lanceolata Cav. Sterculiaceae Sảng nhung Tree
266 Streblus asper Lour. Moraceae Ruối nhám Non-tree
267 Streblus laxiflos (Hutch.) Corner Moraceae Duối rừng Tree
268 Streblus macrophyllus Bl. Moraceae Mạy tèo Tree
269 Streblus tonkinensis (Dub. & Eberh.) Corner Moraceae Teo nông Tree
270 Strychnos angustiflora Benth. Loganiacaea Củ chấy Non-tree
271 Strychnos wallichii Steud. = S. gaulthierana Pierre Loganiacaea Mã tiền dây Non-tree
272 Swietenia macrophylla Meliaceae Dái ngựa Tree
273 Symplocos laurina var. acuminata (Miq) Brand. Symplocaceae Dung giấy Tree
274 Syzygium bullockii (Hance) Merr. et Perry Myrtaceae Trâm voi Tree
275 Syzygium jambos (L.) Alston Myrtaceae Roi rừng Tree
276 Syzygium pachysarcum (Gagn.) Merr. & Perry. Myrtaceae Trâm sánh Tree
277 Syzygium wightianum Wight et Arn. Myrtaceae Trâm trắng Tree
278 Syzygium zeylanicum (L.) DC. Myrtaceae Trâm vỏ đỏ Tree
279 Syzysium senamangense (Bl.) Merr. & Perry. Myrtaceae Mận rừng Tree
280 Taractogenos sp Flacourtiaceae Chùm bao Tree
281 Taxillus chinensis (DC.) Dans. Loranthaceae Hồng tuyến Non-tree
282 Tetracera scandens (L.) Merr Dilleniaceae Dây chặc chìu Non-tree
283 Tetrastigma retinervum Planch. Vitaceae Dây doãn Non-tree
284 Thunbergia eberhardtii R.Ben. Acanthaceae Cát đằng vàng Non-tree
285 Tinospora sagitta (Oliv.) Gagnep Menispermaceae Củ gió Non-tree
286 Tinospora sinensis (Lour.) Merr. Menispermaceae Đơn xương Non-tree
287 Triumfetta bartramia L. Tiliaceae Non-tree
288 Tsoongiodendron odorum Chun Magnoliaceae Giổi lụa Tree
289 Uvaria microcarpa Champ. ex Benth. Annonaceae Dất lông Non-tree
290 Ventilago leiocarpa Benth. Rhamnaceae Dây cốt khí Non-tree
291 Verbesina biflora L Asteraceae Lá mui biển Non-tree
292 Vernonia aff. acumingiana Benth. Asteraceae Thuốc máu Non-tree
293 Vitis balanseana Blume Vitaceae Đậu xương Non-tree
294 Vittaria ensiformis Sw. Thelypteridaceae Quyết dương xỉ Non-tree
295 Wendlandia paniculata (Roxb.) DC. Rubiaceae Hoắc quang trắng Tree
296 Wrightia tomentosa (Roxb.) Roem. & Schult. Apocynaceae Thừng mực Tree
297 Wrightia laevis Hook.f. Apocynaceae Thừng mực mỡ Tree
298 Xerospermum noronhianum Blume. Sapindaceae Vải rừng Tree
299 Zanthoxylum nitidum (Lamk.) DC. Rutaceae Sẻn gai Tree
300 Zephyranthes carinata Herb Amaryllidaceae Tóc tiên Non-tree
301 Zizyphus eonoplia (L) Mill. Rhamnaceae Táo rừng Tree
302 Zizyphus incurva Roxb. Rhamnaceae Táo vòng Tree
login to comment