Conservation priorities and distribution patterns of vascular plant species along environmental gradients in Aberdare ranges forest
expand article infoSolomon Kipkoech§|, David Kimutai Melly§|, Benjamin Watuma Mwema§|, Geoffrey Mwachala, Paul Mutuku Musili, Guangwan Hu§|, Qingfeng Wang§|
‡ East African Herbarium, National Museums of Kenya, Nairobi, Kenya
§ Wuhan Botanical Garden, Chinese Academy of Sciences, Wuhan, China
| University of Chinese Academy of Sciences, Beijing, China
¶ Sino-Africa Joint Research Center, Chinese Academy of Sciences, Wuhan, China
Open Access


Distribution patterns of biodiversity and the factors influencing them are important in conservation and management strategies of natural resources. With impending threats from increased human population and global climatic changes, there is an urgent need for a comprehensive understanding of these patterns, more so in species-rich tropical montane ecosystems where little is known about plant diversity and distribution. Vascular species richness along elevation and climatic gradients of Aberdare ranges forest were explored. A total of 1337 species in 137 families, 606 genera, 82 subspecies and 80 varieties were recorded. Correlations, simple linear regression and Partial least square regression analysis were used to assess richness and diversity patterns of total plants, herbs, shrubs, climbers, arboreal and endemic species from 2000–4000 m above sea level. Total plant species richness showed a monotonic declining relationship with elevation with richness maxima at 2000–2100 m a.s.l., while endemic species richness had a positive unimodal increase along elevation with peaks at 3600–3700 m a.s.l. Herbs, shrubs, climbers and arboreal had significant negative relationships with altitude, excluding endemism which showed positive relations. In contrast, both air and soil temperatures had positive relationships with taxa richness groups and negative relations with endemic species. Elevation was found to have higher relative influence on plant richness and distribution in Aberdare ranges forest. For effective conservation and management of biodiversity in Aberdare, localized dynamic conservation interventions are recommended in contrast to broad and static strategies. Establishment of conservation zones and migration corridors are necessary to safeguard biodiversity in line with envisaged global climatic vicissitudes.


Aberdare ranges, conservation, elevation, species richness, temperature, vascular plants


Tropical afromontane ecosystems are renowned hotspots of biological diversity often with significant numbers of endemic species (Mittermeier et al. 1998; Lovett et al. 2005; Sosef et al. 2017). A combination of non-random climatic and abiotic gradients, and evolutionary processes in montane forests have been reported to influence the myriad distribution patterns and composition of plants’ communities found along these mountains (Lomolino 2001). Since montane ecosystems are small and isolated from other similar ecosystems, plant communities in these regions face relatively high extinction rates and low immigration rates (Newmark and McNeally 2018). Therefore, to sustainably manage and conserve these ecosystems an authentic conceptual framework (comprehensive understanding) of species richness and distribution patterns is a prerequisite (Lovett et al. 2005; Sosef et al. 2017; Anderson-Teixeira 2018) . According to Dyakov (2010), plant species are distributed in variable habitats but are most abundant in areas which represent their ecological optimum. Also, Lovett (1999) argued that these plants’ composition and distribution patterns reflect the underlying anthropogenic disturbances. Therefore, an understanding of these patterns can be used to prioritize regions that either need immediate or different management interventions so as to conserve the targeted species.

Previous studies have reported a significant relationship between elevation and plant communities, indicating that elevation is a strong predictor of vegetation structure and richness (Lomolino 2001, Berhanu et al. 2017). However, the extent of its influences remains unclear since it has both indirect effect on species richness and direct effects on environmental complexes (i.e., temperature, growing season, precipitation, wind velocity, atmospheric pressure and evaporation) which are also crucial in spatial patterns of plants (Whittaker 1967; Blundo et al. 2012; Dyakov 2014). Thus, the trends observed in spatial patterns on a mountainous ecosystem cannot be explained by a single factor but rather by an interaction of multiple factors (Lee et al. 2013; Trigas et al. 2013). The effects of these environmental factors are dynamic and vary among different plant groups and growth forms (Zhou et al. 2019). Bhattarai and Vetaas (2003) found significant trends between woody life forms and elevation gradient, but none among the herbaceous species of the Himalayas in Nepal. Dissimilar distribution of plant communities in relation to environmental gradients has been described in many studies (Hamilton and Perrott 1981; Lovett 1996; Grytnes and Vetaas 2002; Vetaas and Grytnes 2002; Bhattarai and Vetaas 2003; Schmitt et al. 2010; Lee et al. 2013; Trigas et al. 2013; Berhanu et al. 2017).

The Aberdare ranges present an interesting ecosystem in that the northern part of this forest is almost at the equator and the western slopes form part of the easternmost wall of the Gregory Rift valley (Schmitt 1991; Bennun and Njoroge 1999). It is one of the five major water catchment towers in Kenya with three major rivers emanating from this forest, i.e. the Tana, Athi and Ewaso Ng’iro rivers (Muiruri 1978; KFS 2010). Overall, the Aberdare forest provides invaluable social, economic and environmental benefits with estimates indicating that at least one in three people in Kenya depends in some way on the natural resources from this ecosystem (Ark and Group 2011; Rhino 2016). These ranges are renowned for their geographically diverse taxa and high endemism (Hedberg 1964; Hedberg and Hedberg 1979) due to wide elevational gradient and other biotic and abiotic factors (Schmitt 1991; Lambrechts et al. 2003; KFS 2010). The heterogeneous flora along the altitude breath stands out as unique biota above the warmer plains surrounding these volcanoes (Hedberg and Hedberg 1979). Despite its complex vegetation diversity, little has been done to quantify the species richness, composition and altitudinal turnover in this afromontane forest. This study, therefore, aimed at describing the overall floral richness patterns and identify areas with strikingly unique richness so as to provide a baseline framework for immediate or future localized and effective conservation strategies. The specific objectives of the study were to (a) investigate the distribution patterns of the plants, herbs, shrubs, climbers, arboreal and endemic species in Aberdare ranges, (b) explore the degree of influence of elevation, air and soil temperatures on the richness patterns of the same taxon groups, and (c) evaluate conservation priorities based on observed species richness and distribution patterns for the entire Aberdare ecosystem.

Materials and methods

Study site

The study was carried out in the Aberdare mountains, located in central parts of Kenya (Bennun and Njoroge 1999). It stretches for 120 km from north to south from latitude 00°08' to 00°42' south, with an expanse of about 40 km across at its widest point between longitude 36°31' to 35°57' east (Butynski 1999) (Fig. 1). The Aberdare ranges are characterized by undulating hills formed through uplift and warping, then later shaped by volcanism and faulting of the earth surface from early Tertiary to the Pleistocene (Peltorinne 2004), giving rise to geographically isolated islands of complex tropical-alpine vegetation (Hedberg 1964). There are two main peaks; Oldonyo Lesatima (4000 m a.s.l.) to the north and Il Kinangop (3906 m a.s.l.) to the south, separated by a long stretch of land above 3000 m elevation (Muiruri 1978; Bennun and Njoroge 1999). Aberdare exhibits a unique topography sloping gradually to the East while, in contrast, the western slopes drop rapidly along imposing fault escarpments towards the Kinangop plateau and finally the Gregory Rift Valley, giving way to a number of torrential waterfalls that cascade into deep u-shaped ravines (KFS 2010; KWS 2010).

Figure 1. 

The location of Aberdare ranges forest, (i) two sections of forest (ii) map of Kenya.

Similar to other East African mountains, vegetation in Aberdare is typical afromontane type characterized by heterogeneous vegetation structure along the elevational gradients (Hedberg 1951; Myers et al. 2000). Three broad vegetation zonations have been described by Schmitt (1991) based on floristic compositions, including the montane forest belt at lower altitudes, the subalpine zone at mid elevation, and the alpine zone at the summit. Administratively, this forest is managed in two sections, i.e., Aberdare national park, size ca. 76700 ha., managed by Kenya Wildlife Service (KWS), and Aberdare forest reserve, size ca. 139500 ha., governed by Kenya Forest Service (KFS). The national park is situated at higher elevations above ca. 2600 m a.s.l. and the regions below this park constitute the forest reserve composed of three forest blocks, Aberdare, Kikuyu escarpment, and Kipipiri forest reserve (KWS 2010; KFS 2010, Lambrechts et al. 2003). Altitude is from 1800 m to 4000 m a.s.l. (Bennun and Njoroge 1999). Climate in Aberdare forest is dominated by the passage of the Inter-Tropical Convergence Zone north and south during its annual cycle, producing a bimodal rainfall distribution (CEPF 2012). Long rains usually come from March to May and short rains from October to November (Lambrechts et al. 2003; KFS 2010). Annual rainfall varies with altitude and exposure to the dominant winds from the Indian Ocean, ranging from 1000 mm on the drier north-western slopes to as much as 3000 mm on the south-eastern slopes (Bennun and Njoroge 1999). The mean maximum temperature is 25.8 °C. while mean minimum temperature is 10.3 °C. (KFS 2010; CEPF 2012).

Data Sources

The floristic surveys were carried out from the year 2016 to 2018, during the optimum flowering and fruiting periods which were mainly after the long and short rains of March-May and November-December respectively. A team of botanists from the National Museums of Kenya and Sino-Africa Joint Research Center undertook the surveys. Fertile voucher plant specimens, with either flower, fruit or both were collected, pressed, and dried. Specimens were identified to species level using varied taxonomic monographs and botanical guide books (FTEA 1952–2012; Blundell 1992; Agnew and Agnew 1994; Beentje et al. 1994; Agnew 2013). Plant species were further categorized into their life forms, including (i) herbs (plants less than 50 cm or less than 100 cm but annual), (ii) shrubs (plants between 50cm to 5 m tall), (iii) climbers (plants with twining herbaceous or woody stems), and (iv) arboreal (plants taller than 5m) (Raunkiaer 1934, Schmitt 1991, Bao et al. 2018). Finally, the dried voucher specimens were deposited in the East African Herbarium (EA), Nairobi, and Wuhan Botanical Garden herbarium (HIB), China.

Endemic species were recorded from published literature and updated by cross-checking with the online occurrence data in Global Biodiversity Information Facility (GBIF) ( In addition to field collections, other plant species in Aberdare ranges forest were obtained from the previously collected specimens in the EA herbarium catalogues, series of Flora of Tropical East Africa (FTEA) and other standard references (e.g., Schmitt 1991). Relative altitude range sizes of plant species in Aberdare i.e., the maximum and minimum altitude where a species has been previously recorded or collected, were determined from our collections, as well as from other specimens in the EA herbarium and the standard botanical references. Based on the contemporary description of the Flora of Kenya, information on the floral species and their geographical distributions was considered adequate for this study.

Both air and soil temperature data were obtained from Schmitt (1991), where he calculated the average air temperature from 28 months’ recordings from four locations at different altitudes in Aberdare ranges. Extrapolation was done based on a calculation from East African Meteorological Department (1970) of a decrease of 1.7 °C. for every 1000 feet of altitude equivalent to 0.56 °C. per 100 m elevation. Regarding the soil temperature, Schmitt (1991) obtained the mean of 9 months recordings at 70 cm depth of soil in eight different elevations in the Aberdare ranges. He calculated an average of 0.52 °C. decrease per 100m elevation between 1900−3200 m a.s.l. and 1.5 °C. decrease per 100 m between 3200−3600 m a.s.l. (Braun 1986; Schmitt 1991). This criterion was applied to calculate soil temperatures at altitude bands where there were no recordings.

Data analysis

The Aberdare mountain rises from 1800−4000 m a.s.l. However, the onset of continuous forest cover differs in elevation at various sites of forest edges. To control the biases of uneven elevation of forest margins and disjunct forest blocks, we analyzed species from 2000−4000 m a.s.l. as this represents relatively the continuous forest cover in the entire ecosystem (Schmitt 1991, Butynski 1999). Elevation gradient was divided into 20 bands of 100 m interval between the 2000−4000 m altitude in the same manner as Vetaas and Grytnes (2002), Bhattarai et al. (2004) and Grau et al. (2007). Recorded plant species were then interpolated at these 20 100 m bands giving an estimate of gamma diversity defined by Lomolino (2001) as total richness of an entire elevation band. The assumption here was that each species was present in all the elevation bands within its altitude range size, ignoring any disjunctions in its distribution along elevation gradient. Interpolation of species facilitates analysis where there is incomplete sampling as in this study. A comparative analysis conducted on empirical and interpolated species richness data of the Baekdudaegan mountains of South Korea showed similar spatial distribution patterns (Lee et al. 2013). Hence interpolation of taxon richness was best suited for our study as it can give reliable results similar to complete sampling. Each plant species, subspecies or varieties were treated as individual taxa. The relationship between all these plant groups and elevation, air temperature and soil temperature were investigated in IBM SPSS statistic 25 software.

Descriptive statistics were explored to interpret data distributions and normality tests (Table 1). Moderate skewness and negative kurtosis were observed indicating nearly normal distributions as they were below 1 and 2.5 respectively (Zhao and Fang 2006). Arboreals were square-root transformed since it failed Kolmogorov-smirnov normality tests (P < 0.023). No transformations were done for other groups as their distributions were normal (P > 0.05). Simple scatter plots were used to observe if non-linear relationship existed between plant groups and combined environmental variables studied. All plant groups showed linear relationship, hence Pearson’s Correlation analysis was done. Multiple regression model was best suited for data analysis, however, there was significant multicollinearity between the predictors (r > 0.07), which would have given unreliable results. Therefore, Partial Least Squares (PLS) regression model was used (Tobias 1995). PLS regression is robust in multicollinear variables and it focuses on components with maximum covariance with dependent variable (Maestre 2004; Davis et al. 2007; Carrascal et al. 2009), hence, an environmental factor with the highest projection on richness patterns of plants groups could be identified through this model. Relative importance of individual predictor was evaluated using Variable Importance in Projection (VIP) values i.e., the higher the VIP the higher the importance in projection. PLS regression with a Python 2.7 extension module was used in IBM SPSS statistic 25 software. In addition to PLS regression, simple linear regression of each environmental factor on each studied plant group was also calculated.

Table 1.

Summary of descriptive statistics of environmental factors and vascular plants groups in Aberdare ranges forest.

Variables N Minimum Maximum Mean SD Skewness Kurtosis K-S (P)
Environmental factors
Elevation 20 2050 3950 3000 132.288 0 -1.200 0.2
Air temperature 20 3.86 16.58 9.73 4.129 0.393 -1.063 0.2
Soil temperature 20 1.3 18.02 11.47 5.098 -0.602 -0.763 0.2
Species richness
Total plants 1337 171 1032 593.15 62.952 0.087 -1.401 0.2
Endemic species 63 20 37 28.35 6.124 0.027 -1.737 0.124
Plant Life forms
Herbs 888 144 691 446.25 191.877 -0.224 -1.443 0.2
Climbers 101 2 83 33.15 28.372 0.424 -1.349 0.095
Shrubs 198 24 151 76.05 41.19 0.572 -0.997 0.135
Arboreal 150 1 116 37.7 38.811 0.996 -0.408 0.023


The Aberdare ranges forest has high plant diversity. The majority of the plants recorded were seed plants totaling 1255 taxa including forbes while 86 were ferns. The top-ranking families as per the number of taxa were Asteraceae 11%, Poaceae 8%, Fabaceae 7%, Lamiaceae 4%, Cyperaceae 4%, Rubiaceae 4%, Euphorbiaceae 3% and Orchidaceae 3%. Other families had fewer species with some having a single species. According to plant life forms, most taxa were herbs 64.2%, then shrubs 11.9%, arboreal 11.5% and climbers were 7.5% of the total taxa recorded (Fig. 2). Endemic species composed of varied life forms were 4.7% of the total taxa recorded. Average altitude range for total taxa excluding endemic species was 1585 m. Among the life forms, herbs had the highest average altitude range at 1614 m, climbers 1578 m, shrubs 1490 m, and the lowest was arboreal at 1350 m. Endemic species had the lowest average altitude range of 1139 m.

Figure 2. 

Proportions of endemic and non-endemic plants species life forms. (E – endemics, NE – non endemics).

Pearson’s correlation analysis showed significant relationship between total plants, endemic species, life forms groups and environmental variables (see Table 2). Elevation had negative correlation with herbs, shrubs, climbers and arboreal. Total plants also had negative correlation with elevation but endemic species showed a weak positive relationship. Both air and soil temperatures showed significant positive relations with all life form groups. Endemic species had negative correlations with air and soil temperature while total plants had positive relationship with both temperatures. Simple linear regression indicated variations in richness patterns of the studied taxa groups. Elevation explained 99.3% of total plant richness and 69.2% for endemic species. Air and soil temperatures also had higher influence on total plant richness explaining 97.4% and 93.2% respectively. Strikingly, temperature variables showed lower prediction on endemic species with just 64.9% explained by air temperature and 58.9% by soil temperatures. In general, all the environmental factors had significant prediction on all life form groups’ richness and distribution patterns (P < 0.000) (Table 2). Soil temperature was found to have the least influence on richness patterns prediction compared to other environmental factors.

Table 2.

Correlation analysis between environmental factors and plant species groups.

Altitude Air temp. Soil temp. Total plants Herbs Shrubs Climbers (Sqrt) Arboreal Ende-mics
Altitude Pearson Correlation 1 -.985** -.977** -.997** -.991** -.975** -.977** -.984** .832**
Sig. (2-tailed) 0.000 0.000 0.000 0.000 0.000 0.000 0.000 0.000
N 20 20 20 20 20 20 20 20
Air temp. Pearson Correlation 1 .938** .987** .963** .992** .982** .994** -.806**
Sig. (2-tailed) 0.000 0.000 0.000 0.000 0.000 0.000 0.000
N 20 20 20 20 20 20 20
Soil temp. Pearson Correlation 1 .965** .984** .912** .913** .932** -.767**
Sig. (2-tailed) 0.000 0.000 0.000 0.000 0.000 0.000
N 20 20 20 20 20 20
Total plants Pearson Correlation 1 .991** .981** .985** .988** -.853**
Sig. (2-tailed) 0.000 0.000 0.000 0.000 0.000
N 20 20 20 20 20
Herbs Pearson Correlation 1 .948** .959** .961** -.844**
Sig. (2-tailed) 0.000 0.000 0.000 0.000
N 20 20 20 20
Shrubs Pearson Correlation 1 .989** .995** -.825**
Sig. (2-tailed) 0.000 0.000 0.000
N 20 20 20
Climbers Pearson Correlation 1 .988** -.877**
Sig. (2-tailed) 0.000 0.000
N 20 20
(Sqrt) Arboreal Pearson Correlation 1 -.828**
Sig. (2-tailed) 0.000
N 20
Endemics Pearson Correlation 1

Total plants showed significant monotonic declining trend with increasing elevation (β = − 0.997, R2 = 0.95). Total plants species richness peaked at 2000−2100 m a.s.l. with 1032 taxa then gradually declined to just 171 taxa at the summit of the mountain. On the contrary, endemic species increased with increasing elevation (β = 0.832, R2 = 0.692) with richness maximum at 3300−3700 m a.s.l., suggesting that endemism was favored in high altitudes with associated harsh climatic conditions. Similar significant monotonic declining trends along the altitude were also observed among the life forms groups; herbs (β = − 0.991, R2 = 0.982), shrubs (β = − 0.975, R2 = 0.950), climbers (β = − 0.977, R2 = 0.954), and aboreals (β = − 984, R2 = 0.983). Trends of life form groups along air and soil temperature gradients are listed in Table 3.

Table 3.

Simple linear regression of altitude, air temperature, soil temperature and each plant group.

Environmental variables Total plants Endemics Herbs Shrubs Climbers Arboreal
Pearson Correlation (r) -0.997 0.832 -0.991 -0.975 -0.977 -0.984
Sig (1-tailed) (p < 0.05) 0.000 0.000 0.000 0.000 0.000 0.000
Model Summary (R2) 0.993 0.692 0.982 0.950 0.954 0.969
Air Temperature
Pearson Correlation (r) 0.987 -0.806 0.963 0.992 0.982 0.994
Sig (1-tailed) (p < 0.05) 0.000 0.000 0.000 0.000 0.000 0.000
Model Summary (R2) 0.974 0.649 0.928 0.984 0.964 0.988
Soil Temperature
Pearson Correlation (r) 0.965 -0.767 0.984 0.912 0.913 0.932
Sig (1-tailed) (p < 0.05) 0.000 0.000 0.000 0.000 0.000 0.000
Model Sum (R2) 0.932 0.589 0.968 0.832 0.833 0.869

PLS regression model indicated the importance of each studied environmental factor in projecting richness patterns among the studied groups. Elevation, air and soil temperatures projected significant richness trends for total plants (R2 = 0.988) and low projection in endemic richness trends (R2 = 0.639). Other proportions of variance explained by our PLS model in herbs, shrubs, climbers and arboreal were also high and significant (Table 4). Elevation was indicated to have the highest relative importance in richness patterns of all the plant groups (V.I.P. > 1) (Maestre 2004). Air temperature showed high relative importance in projection of all studied groups except for the herbs which was slightly below 1 (Table 4). Soil temperature was the least influencing variable overall in all the studied groups. Elevation had negative and positive relationship with total plants and endemic species respectively. In contrast, air and soil temperatures showed positive relationships with total plants and life form groups but negative relations with endemic species It was interesting to note that similar results shown in correlation and simple linear regression analysis were also observed in PLS model.

Table 4.

Partial least square regression of combined environmental factors and species richness groups.

Species Groups Parameters V.I. P W L Proportion of Variances explained (adjusted R2)
Total Plants 0.988
Elevation -0.553 1.014 -0.585 -0.583
Air Temperature 3.423 1.004 0.580 0.575
Soil Temperature -9.427 0.982 0.567 0.574
Endemic species 0.639
Elevation 0.053 1.037 0.599 0.583
Air Temperature 3.241 1.005 -0.580 -0.576
Soil Temperature 2.615 0.957 -0.552 -0.574
Herbs 0.980
Elevation -0.316 1.012 -0.584 -0.583
Air Temperature -10.046 0.984 0.568 0.575
Soil Temperature 8.803 1.005 0.580 0.574
Shrubs 0.941
Elevation -0.066 1.015 -0.586 -0.583
Air Temperature 5.936 1.033 0.596 0.576
Soil Temperature -4.647 0.95 0.548 0.574
Climbers 0.935
Elevation -0.098 1.020 -0.589 -0.583
Air Temperature -0.743 1.025 0.592 0.576
Soil Temperature -5.419 0.953 0.550 0.574
Arboreals 0.962
Elevation -0.005 1.014 -0.586 -0.583
Air Temperature 0.392 1.024 0.591 0.576
Soil Temperature -0.241 0.960 0.555 0.574

Plants of special concern

Aberdare ranges forest harbors a number of globally important plant species. A total of 73 species have been assessed globally to be threatened and 30 species are possibly threatened according to Botanic Gardens Conservation International threat search 2019 ( This is a clear indication of the global importance of Aberdare ranges forest as a biodiversity hotspot and the urgent need for effective conservation measures to protect the threatened species and the rich plant diversity in general. The majority of the threatened species were herbs with 70 species, shrubs 12, climbers 11 and the arboreal numbered 10 (see Appendix 1).


Plant species richness and distribution patterns

Plants diversity in Aberdare ranges is high, based on the total taxa recorded in our study. This was higher than the previous survey done by Schmitt (1991) which documented 778 species in 128 families and 421 genera. Altitude was found to have relatively higher influence on distribution and richness patterns of plant species in this forest. This suggests that the heterogeneous vegetation structure exhibited in the Aberdare ranges is a manifestation of altitude increase. This phenomenon has attracted a lot of debate with several factors mentioned as explanatories for habitat heterogeneity, e.g., energy, water, soils, and area. However, these factors are known to have direct influence on plant physiological processes which in turn control plant growth and spatial richness; at the same time these factors are directly influenced by altitude (Whittaker 1967; Rahbek 1997; Schmitt et al. 2013; Berhanu et al. 2017). Therefore, altitudinal gradient can be regarded as an overall fundamental factor with indirect effects on species richness patterns. Dyakov (2014) argued that altitude can be used to provide insightful information on plants richness and distribution patterns, especially in ecosystems where other abiotic parameters are missing and this notion has been supported by this study. Total plant species in Aberdare showed a monotonic declining relationship with optimum altitude ranging between 2000–2100 m a.s.l., which was simply the foot of the Aberdare ranges. The aggregation of species at lower elevation indicated mass effect which coincided with Rahbek’s (1997) observation that lowlands represent sink habitats with higher species richness than other higher elevation zones. This higher richness is likely due to the infusion of species from surrounding lowland vegetation which could not survive at higher elevations (Rahbek 1997). It is also probable that human transferred species might have been perfectly integrated and naturalized during early historic community settlements in and around Aberdare mountains (Trigas et al. 2013). The known harsh environmental constraints at higher elevations such as cooler temperatures, low energy, shorter growing seasons, solifluction, isolation, etc., could have deterred to an extent any immigration, dispersal and invasiveness of new plant species at these elevated areas (Hedberg 1964; Vetaas and Grytnes 2002; Dyakov 2014). Furthermore, monotonic decline of species richness could be due to the absence of true montane flora in Aberdare, where the current richness patterns are a result of the spread of lowland species that could withstand and adapt to the mentioned harsh conditions associated with higher elevations (Hedberg and Hedberg 1979; Trigas et al. 2013). Numerous studies in similar montane ecosystems have reported monotonic decline of floristic richness. In Ethiopian afromontane vegetation, species richness peaked between 1600–1700 m a.s.l. which was lower than Aberdare despite both mountains flanking the Great Rift Valley (Berhanu et al. 2017). Vetaas and Grytnes (2002), using interpolated data of Nepal Himalayas, found a hump-shaped unimodal relationship with maxima species richness between 1500–2500 m a.s.l., which was similar to this study.

There was a slight increase in richness of herbs between 2000–2100 m a.s.l. then a monotonic decline as altitude increases. Herbs showed higher gamma diversity i.e., total species in each altitude band, compared to other studied plant groups in entire altitude gradient of Aberdare ranges. Regarding this observation, this study contrasted with Schmitt et al. (2010) generalization that herbs are more sensitive to small-scale changes in environmental conditions while woody plants are affected by environmental changes at larger scale. If this was the case then woody species richness i.e., shrubs and arboreal would be more abundant at higher altitudes which was not observed in this study. As floral richness is known to be maximum at altitudes associated with their optimal climatic gradients (Lomolino 2001; Dyakov 2014), based on this study 2000–2200 m a.s.l. seems to be the focal altitude for total plants in Aberdare ranges forest. The effects of heavy deforestation at lower altitudes in close proximity to local communities around the forest (Butynski 1999; Lambrechts et al. 2003; KWS 2010; KFS 2010) were not shown in our study. It was expected that richness in shrubs and arboreal would be low at the foot of the range as a result of overexploitation then a slow or even absent succession by arboreal species afterwards.


A total of 63 species were endemic in Aberdare ranges forest. Most of these endemics were herbs - with 35 species, then shrubs 23, climbers 3 and the lowest were arboreal with 2 species (see Appendix 2). The altitudinal range sizes, i.e., between the minimum and maximum altitude, of these endemic species varied from as low as 100 m for Cissampelos friesiorum Diels, 150 m for Senecio margaritae C.Jeffrey to 2500 m for Adenocarpus mannii (Hook.f.) Hook.f. and Erica sylvatica (Welw. ex Engl.) Beentje. Endemic species had positive relations with elevation and negative relations with both air and soil temperatures. There was a continuous spread of endemic species in the entire forest; however, higher richness was observed at higher altitude. Endemism richness maxima ranged between 3200–3900 m a.s.l., which overlapped with the endemic species of the Himalayas mountain which peaked between 3500–4500 m a.s.l. (Vetaas and Grytnes 2002). This study supported the generalization that endemic species as restricted range taxa were manifested by the survival of species in refugia during Pleistocene climatic fluctuations and/or their resilience and adaptation to unique long-term abiotic conditions that promoted morphological differentiation of relict taxa (Lovett and Friis 1994; Lovett et al. 2000). Higher endemism towards the top of Aberdare ranges might be a result of temporal individual responses of plant species to climatic vicissitudes leading to novel assemblages at high altitudes as different species move individually up the slope (Lovett et al. 2005). There was a notably rapid increase in endemic richness at 2700–3000 m a.s.l. which coincided also with the rapid decrease in total plant species richness. This striking feature was also observed among the endemics of the Himalayas in Nepal although at higher altitudes above 4000 m a.s.l. (Vetaas and Grytnes 2002). The authors at Himalayas Nepal argued that timberline and glaciation limits are responsible for the inverse relationship between endemism and total plant richness. However, this view was only partially supported in our study due to the current absence of glaciers in the Aberdare ranges which are thought to have disappeared during early Holocene glaciation (Young 1980; Rosqvist 1990; Mark and Osmaston 2008). This study therefore suggests that perhaps localized competition among plant species has an effect on endemic richness and diversity although this largely remains a speculative concept. Increasing isolation and decreasing surface area at higher elevation which are responsible for fragmentation of species population, have been argued to facilitate endemism because of the small population’s vulnerability to speciation (Trigas et al. 2013 and references there in). The formation of the Aberdare mountains during the break-up of Gondwanaland millions of years ago led to isolation of plant species that existed then. Over time these species have undergone speciation, resulting in numerous endemic species (Butynski 1999).

Conservation priorities

In the wake of elevated anthropogenic threats and global climatic vicissitudes, conservation and management of Afromontane ecosystems should be prioritized, particularly for future biodiversity and sustainable provision of ecological services (Muiruri 1978; Myers et al. 2000; Hannah et al. 2002; Kiringe et al. 2007; KFS 2010; Schmitt et al. 2010; Di Minin et al. 2013; Anderson-Teixeira 2018). Afromontane forests are thought to provide survival options for plants in a changing climate through the close physical proximity of a wide range of habitats with varied biotic and abiotic factors (Lovett et al. 2005). Thus, the Aberdare ranges with its proven diverse flora and unique physical properties calls for more effective management interventions. Floristic composition and spatial patterns studied in this forest can steer conservation strategies by pinpointing exceptional rich species and ecologically unique zones (Platts et al. 2010). Thence, the type of management regime to be implemented should target the causal factors of observed richness patterns since species richness is an indicator of environment history (Lovett et al. 2000; Platts et al. 2010). This implies that any conservation intervention to be undertaken should focus on maintaining the forms and magnitudes of disturbances the existent vegetation has adapted to. For the case in Aberdare, higher endemic richness at higher elevations indicates the existence of undisturbed long-term environmental stability as argued by Lovett and Friis (1994), Sosef (1994) and Lovett et al. (2000). Therefore, disturbances should be minimized at this zone because the vegetation might not be resilient to perturbation. Networks of roads and camp sites should be reduced, if not totally eliminated, in upper parts of the forest (KFS 2010; KWS 2010). According to Connell (1978), Phillips et al. (1994) and Lovett et al. (2000) high species diversity is a result of intermediate levels of disturbance that enhances recruitment and regeneration of new species. If this concept of disturbance-driven species richness is applied at lower elevations of Aberdare, where there is a history of exploitation by local community (Butynski 1999), then it means that the great species richness observed at this region could be due to disturbance. Therefore, a suitable management intervention should complement the previous disturbances at appropriate levels and magnitude so as to maintain plant species complementation. This will necessitate some controlled small-scale extraction and utilization of forest resources around the foot of Aberdare ranges. Regulated extraction and utilization of forest products could be the best conservation strategy at species level as this can be an intermediate disturbance if well managed. The carrying capacity of the vegetation area to be grazed should be established prior to grazing.

In view of envisaged climatic changes, it has been suggested that ecosystems migrate to new regions as a result of climatic fluctuations (Hannah et al. 2002; Lovett et al. 2005). In fragmented ecosystems characterized by isolated habitats that are surrounded by agricultural or other human activities, such ecosystems will have no room for migration resulting in total collapse (Hannah et al. 2002). This scenario resonates with the present situation in the Aberdare ranges with agricultural activities surrounding the forest almost entirely. To overcome the impending predicament of ecosystem collapse, creation of corridors seems to be the best strategy, perhaps the only way, to facilitate ecosystem migration and enhance survival of species (Lovett et al. 2005).

Completion of a perimeter electric fence around the Aberdare ranges almost a decade ago has impacted significantly on both ecological and economic aspects of this region (Ark and Group 2011). However, the long-term effects of this fence regarding migration and population increase of wildlife, particularly the large herbivores, have not been adequately addressed (Butynski 1999; Ark and Group 2011). A complete barrier to the migration of elephants has increased damage to vegetation mostly around their traditional migratory routes to the lower Laikipia savanna and Mount Kenya (Ark and Group 2011). Prolonged damage to vegetation in such areas will result in larger open grounds with reduced plant diversity which will lead to minimal utilization of nutrients by plants since the full range of plant niches is not covered (Lovett et al. 2005). This unbalanced destruction of vegetation in the Aberdare ranges will disrupt its ecological equilibrium and threaten the ecosystem functioning and sustainability in the long run (Tilman et al. 1996, 2006). In addition, the expanding populations of range-restricted elephants and other herbivores will increase vegetation damage in the near future. A management intervention in this respect should be at vegetation level and must aim at balancing utilization and regeneration of resources to maintain adequate vegetation cover and rich species diversity, thus maintaining ecological balance and ecosystem productivity of the Aberdare range forest. Migratory corridors should be established, perhaps along the traditional migratory routes, to facilitate seasonal migration of large herbivores in an out of Aberdare ranges.

Wildfires in the Aberdare ecosystem have been common incidences for past decades, occurring mostly during dry seasons in the months of January, February or March and a few cases in September (KFS 2010; KWS 2010). Causes of these fires vary from arsonist ferrying poles, charcoal burning, nearby litter burning during farmland preparations, camp fires and improper cigarette butt disposal by tourists (KFS 2010; KWS 2010; Njeri et al. 2018). Vegetation damages caused by fire are higher at the upper parts of Aberdare including the established plantations due to higher fuel biomass (Njeri et al. 2018). As a result, fragile habitats like the moorland which harbors high endemic and threatened species are negatively impacted. However, fires have also been found to facilitate regeneration of Juniperus procera Hochst. ex Endl., Bambusa vulgaris Schrad, Hagenia abyssinica (Bruce ex Steud.) J.F.Gmel. including some Pines, Cypress and Eucalyptus trees (KFS 2010; KWS 2010; Nyongesa and Vacik 2018). Therefore, the current management approach of prevention and suppression of fire implemented by the KWS and KFS in Aberdare is feasible in the moorland but misplaced in areas with fire-dependent plant species. This study recommends the implementation of an Integrated Fire Management (IFM) framework proposed by Nyongesa and Vacik (2018) in Mount Kenya forest as they are similar ecosystems. In IFM framework, fire-sensitive sites are protected while prescribed-burning is undertaken in fire-dependent ecosystems.


Aberdare ranges forest is exceptionally rich with diverse flora and high endemic species. Floral richness in the entire mountain monotically declined along elevation and temperature gradients. Similar declines of richness were also depicted by the plant life form groups suggesting that growth forms can serve as surrogates for spatial physiognomy of plants that can guide in prioritizing specific areas for conservation (Acharya et al. 2011). Endemic species, by contrast, increased along the studied environmental gradients with richness maxima at higher elevations. The sharp increase of endemism at mid elevations coinciding with rapid reduction in total plant richness raises doubt on the role of competition in the evolution of endemic novelties.

In summary, the Aberdare ranges forest is composed of strikingly diverse flora uniquely distributed along elevational and temperature gradients. Observed richness and distribution patterns in the entire Aberdare range can provide tentative estimates for conservation importance (Acharya et al. 2011). For effective conservation and management of this ecosystem, both natural and human-induced changes should be put into consideration, and a dynamic site-specific management intervention be implemented rather than broad static interventions. This study proposes subdivision of the Aberdare ranges forest into conservation zones where different management programs can be implemented at specific zones based on the characteristics and composition of vegetation in those zones. Further, the study recommends enrichment planting with native species along with exotic species in attempts to rehabilitate heavily deforested patches in the Aberdare ranges forest. Exotic species including Cupressus lusitanica Mill, Pinus patula Schiede ex Schltdl. & Cham. and Juniperus procera Hochst. ex Endl. have been planted to about 35, 444 ha without enrichment planting (Butynski 1999). It has been found that the establishment of exclusively exotic species does not accelerate natural succession in degraded lands due to absence of native species (Mosandl and Günter 2008). Therefore, subsequent enrichment planting with native species after plantations of exotic species will likely accelerate restoration of biodiversity especially if animal-dispersed species are planted in Aberdare ranges forest (Mosandl and Günter 2008).


This study was supported by grants from the Backbone Talents Project of Wuhan Botanical Garden, CAS (Y655301M01) and from Sino-Africa Joint Research Center, CAS (SAJC201614). Much gratitude goes to the National Museums of Kenya, the East Africa Herbarium (EA) for provision of specimens for data extraction as well as preservation of our collected voucher specimens. We acknowledge the National Commission of Science, Technology and Innovation (NACOSTI), Kenya Forest Service (KFS) and Kenya Wildlife Service (KWS) for granting research permits and providing security during floristic surveys.


  • Agnew ADQ (2013) Upland Kenya wild flowers and ferns, third edition. Nature Kenya Publications, Nairobi.
  • Agnew A, Agnew S (1994) Kenya upland wild flowers, second edition. East African Natural History, Nairobi.
  • Bao F, Leandro TD, Rocha MD, Santos VS, Stefanello TH, Arruda R, Arnildo P, Damasceno-Junior GA (2018) Plant species diversity in a Neotropical wetland: Patterns of similarity, effects of distance, and altitude. Anais da Academia Brasileira de Ciências 90(1): 85–97.
  • Beentje H, Adamson J, Bhanderi D (1994) Kenya trees, shrubs, and lianas. National Museums of Kenya, Nairobi.
  • Berhanu A, Woldu Z, Demissew S (2017) Elevation patterns of woody taxa richness in the evergreen Afromontane vegetation of Ethiopia. Journal of Forestry Research 28(4): 787–793.
  • Bhattarai KR, Vetaas OR (2003) Variation in plant species richness of different life forms along a subtropical elevation gradient in the Himalayas, East Nepal. Global Ecology and Biogeography 12(4): 327–340.
  • Blundell M (1992) Wild flowers of East Africa (Collins photo guide). Harper Collins Publishers, London, 21–301.
  • Blundo C, Malizia LR, Blake JG, Brown AD (2012) Tree species distribution in Andean forests: Influence of regional and local factors. Journal of Tropical Ecology 28(1): 83–95.
  • Braun HMH, National Agricultural Laboratories, Kenya Soil Survey (1986) Some characteristics and altitude relationships of temperatures in Kenya. Kenya Soil Survey, Nairobi.
  • Butynski T (1999) Aberdares National Park and Aberdares Forest Reserves wildlife fence placement study and recommendations. Unpublished report to the Kenya Wildlife Service and the Kenya Forest Department, Nairobi.
  • Di Minin E, Macmillan DC, Goodman PS, Escott B, Slotow R, Moilanen A (2013) Conservation businesses and conservation planning in a biological diversity hotspot. Conservation Biology 27(4): 808–820.
  • Dyakov NR (2014) Gradient analysis of vegetation on the south slope of Vitosha Mountain, Southwest Bulgaria. Applied Ecology and Environmental Research 12(4): 1003–1025.
  • East African Meteorological Department (1970) Temperature data for stations in East Africa: Part I Nairobi.
  • Grau O, Grytnes JA, Birks H (2007) A comparison of altitudinal species richness patterns of bryophytes with other plant groups in Nepal, Central Himalaya. Journal of Biogeography 34(11): 1907–1915.
  • Grytnes JA, Vetaas OR (2002) Species richness and altitude: A comparison between null models and interpolated plant species richness along the Himalayan altitudinal gradient, Nepal. American Naturalist 159(3): 294–304.
  • Hamilton A, Perrott R (1981) A study of altitudinal zonation in the montane forest belt of Mt. Elgon, Kenya/Uganda. Vegetatio 45(2): 107–125.
  • Hedberg O (1951) Vegetation belts of East African mountains. Stockholm: Svenska botaniska fôreningens.
  • Kiringe JW, Okello MM, Ekajul SW (2007) Managers’ perceptions of threats to the protected areas of Kenya: Prioritization for effective management. Oryx 41(3): 314–321.
  • Lee CB, Chun JH, Song HK, Cho HJ (2013) Altitudinal patterns of plant species richness on the Baekdudaegan Mountains, South Korea: Mid-domain effect, area, climate, and Rapoport’s rule. Ecological Research 28(1): 67–79.
  • Lovett JC (1996) Elevational and latitudinal changes in tree associations and diversity in the Eastern Arc mountains of Tanzania. Journal of Tropical Ecology 12(5): 629–650.
  • Lovett JC, Friis I (1994) Some patterns of endemism ın the tropıcal north east and eastern African woody flora. In The bıodıversıty of Afrıcan plants, Proceedıngs XIVth AETFAT Congress 22–27.
  • Lovett JC, Rudd S, Taplin J, Frimodt-Møller C (2000) Patterns of plant diversity in Africa south of the Sahara and their implications for conservation management. Biodiversity and Conservation 9(1): 37–46.
  • Maestre FT (2004) On the importance of patch attributes, environmental factors and past human impacts as determinants of perennial plant species richness and diversity in Mediterranean semiarid steppes. Diversity & Distributions 10(1): 21–29.
  • Mark BG, Osmaston HA (2008) Quaternary glaciation in Africa: Key chronologies and climatic implications. Journal of Quaternary Science. Published for the Quaternary Research Association 23(6‐7): 589–608.
  • Mittermeier RA, Myers N, Thomsen JB, Da Fonseca GA, Olivieri S (1998) Biodiversity hotspots and major tropical wilderness areas: Approaches to setting conservation priorities. Conservation Biology 12(3): 516–520.
  • Myers N, Mittermeier RA, Mittermeier CG, Da Fonseca GA, Kent J (2000) Biodiversity hotspots for conservation priorities. Nature 403(6772): 853–858.
  • Newmark WD, McNeally PB (2018) Impact of habitat fragmentation on the spatial structure of the Eastern Arc forests in East Africa: Implications for biodiversity conservation. Biodiversity and Conservation 27(6): 1387–1402.
  • Njeri WF, Githaiga J, Mwala AK (2018) The effects of fires on plants and wildlife species diversity and soil physical and chemical properties at Aberdare Ranges, Kenya. Asian Journal of Forestry 2(1): 25–38.
  • Phillips OL, Hall P, Gentry AH, Sawyer S, Vasquez R (1994) Dynamics and species richness of tropical rain forests. Proceedings of the National Academy of Sciences of the United States of America 91(7): 2805–2809.
  • Platts PJ, Ahrends A, Gereau RE, McClean CJ, Lovett JC, Marshall AR, Pellikka PKE, Mulligan M, Fanning E, Marchant R (2010) Can distribution models help refine inventory‐based estimates of conservation priority? A case study in the Eastern Arc forests of Tanzania and Kenya. Diversity & Distributions 16(4): 628–642.
  • Raunkiaer C (1934) The life forms of plants and statistical plant geography; being the collected papers of C. Raunkiaer. The life forms of plants and statistical plant geography; being the collected papers of C. Raunkiaer.
  • Schmitt K (1991) The vegetation of the Aberdare National park, Kenya. Wagner, Innsbruck (Hochgebigsforschung) 7: 1–250.
  • Schmitt CB, Denich M, Demissew S, Friis I, Boehmer HJ (2010) Floristic diversity in fragmented Afromontane rainforests: Altitudinal variation and conservation importance. Applied Vegetation Science 13(3): 291–304.
  • Schmitt CB, Senbeta F, Woldemariam T, Rudner M, Denich M (2013) Importance of regional climates for plant species distribution patterns in moist Afromontane forest. Journal of Vegetation Science 24(3): 553–568.
  • Sosef MS, Dauby G, Blach-Overgaard A, Van Der Burgt X, Catarino L, Damen T, Deblauwe V, Dessein S, Dransfield J, Droissart V, Duarte MC, Engledow H, Fadeur G, Figueira R, Gereau RE, Hardy OJ, Harris DJ, Heij JD, Janssens S, Klomberg Y, Ley AC, Mackinder BA, Meerts P, Van de Peol JL, Sonke B, Stevart T, Stoffelen P, Svenning JC, Sepulchre P, Zaiss R, Wieringa JJ, Couvreur TLP (2017) Exploring the floristic diversity of tropical Africa. BMC Biology 15(1): 15.
  • Tilman D, Wedin D, Knops J (1996) Productivity and sustainability influenced by biodiversity in grassland ecosystems. Nature 379(6567): 718 pp.
  • Tilman D, Reich PB, Knops JM (2006) Biodiversity and ecosystem stability in a decade-long grassland experiment. Nature 441(7093): 629–632.
  • Trigas P, Panitsa M, Tsiftsis S (2013) Elevational gradient of vascular plant species richness and endemism in Crete-the effect of post-isolation mountain uplift on a continental island system. PLoS One 8(3): e59425.
  • Vetaas OR, Grytnes JA (2002) Distribution of vascular plant species richness and endemic richness along the Himalayan elevation gradient in Nepal. Global Ecology and Biogeography 11(4): 291–301.
  • Young J (1980) The glaciers of East Africa. Paper presented at the World Glacier Inventory (Proceedings of the Workshop at Riederalp, Switzerland 17–22 September 1978). International Association of Hydrological Sciences, Publication.
  • Zhou Y, Ochola AC, Njogu AW, Boru BH, Mwachala G, Hu G, Xin H, Wang Q (2019) The species richness pattern of vascular plants along a tropical elevational gradient and the test of elevational Rapoport’s rule depend on different life‐forms and phytogeographic affinities. Ecology and Evolution 9(8): 4495–4503.

Appendix 1

Plants of special concern in Aberdare ranges forest

Family Plant species Conservation status Life form Altitude range
(m a.s.l.)
Acanthaceae Asystasia lorata Ensermu Kelbessa threatened herb 1400−2000
Amaranthaceae Chenopodium murale L. threatened herb 1070−2750
Chenopodium opulifolium Schrad.U threatened herb 760−2100
Anacardiaceae Rhus longipes Engl. threatened shrub or tree 1000−2400
Apiaceae Torilis arvensis Link possibly threatened herb 1560−2850
Apocynaceae Carissa spinarum L possibly threatened shrub 0−2250
Cynanchum viminale (L.) Bassi threatened herbaceous climber 100−2200
Pentarrhinum abyssinicum subsp. angolense (N.E.Br.) S.Liede & A.Nicholas threatened herbaceous climber 1400−2200
Araliaceae Polyscias kikuyuensis Summerh. possibly threatened tree 1750−2620
Asparagaceae Asparagus racemosus Willd. near threatened woody climber 1160−2900
Aspleniaceae Asplenium adamsii Alston possibly threatened herb 2400−3400
Asplenium aethiopicum (Burm.f.) Becherer threatened epiphyte 1150−3700
Asplenium monanthes L. threatened herb 1950−3400
Asplenium rutifolium (P. J. Berg.) Kunze threatened epiphyte 750−2300
Basellaceae Basella alba L. threatened herbaceous climber 0−2450
Bignoniaceae Jacaranda mimosifolia D. Don threatened tree 1970−1970
Boraginaceae Cynoglossum lanceolatum Forskál threatened herb 1100−3220
Heliotropium zeylanicum (Burm. fil.) Lam. threatened herb 0−1740
Brassicaceae Barbarea intermedia Boreau threatened herb 3050−3950
Cardamine africana L. threatened herb 1000−3400
Farsetia stenoptera Hochst. threatened herb 500−1700
Thlaspi alliaceum L. threatened herb 3050−3600
Campanulaceae Lobelia bambuseti R.E.Fr. & T.C.E.Fr. possibly threatened shrub 2350−4000
Canellaceae Warburgia ugandensis Sprague threatened tree 1100−2230
Cannabaceae Celtis africana Burm. fil. threatened tree 30−2400
Caprifoliaceae Valerianella microcarpa Loisel. possibly threatened herb 2800−3500
Caryophyllaceae Corrigiola litoralis L. threatened herb 1200−2190
Drymaria cordata (L.) Roem. & Schult. possibly threatened herb 870−2700
Uebelinia crassifolia T. C. E. Fries possibly threatened herb 2500−4000
Celastraceae Hippocratea goetzei Loes. threatened climber 0−3000
Asteraceae Ethulia scheffleri S.Moore threatened herb or subshrub 1500−2500
Gynura campanulata C.Jeffrey threatened herb 1600−1615
Asteraceae Helichrysum ellipticifolium Moeser threatened herb or subshrub 2500−4800
Hypochaeris glabra L. threatened herb 1850−3000
Lactuca inermis Forssk. possibly threatened herb 500−3300
Laphangium luteoalbum (L.) N.N.Tzvel. threatened herb 300−3850
Microglossa pyrifolia (Lam.) O. Kuntze possibly threatened shrub 50−2650
Senecio amplificatus C.Jeffrey threatened herb 2900−3500
Solanecio angulatus (Vahl) C. Jeffrey threatened herbaceous climber 1800−2500
Convolvulaceae Cuscuta australis Hook.fil. threatened herbaceous climber 1750−2170
Ipomoea wightii (Wall.) Choisy threatened herb 1040−2400
Cucurbitaceae Peponium vogelii (Hook. fil.) Engl. threatened herbaceous climber 10−2600
Cupressaceae Cupressus lusitanica Mill. possibly threatened tree 2600−2640
Cyperaceae Carex monostachya A.Rich. threatened herb 2700−4500
Carex phragmitoides Kük. threatened herb 2500−3100
Carex vallis-rosetto K.Schum. threatened herb 1000−3300
Cyperus afroalpinus Lye possibly threatened herb 1000−3000
Fimbristylis complanata subsp. keniaeensis (Kük.) Lye possibly threatened herb 1500−2700
Fimbristylis ovata (Burm.f.) J.Kern possibly threatened herb 0−2200
Dennstaedtiaceae Hypolepis goetzei Hieron. ex Reimers threatened herb 2100−3050
Dichapetalaceae Dichapetalum madagascariense (Dup.-Thou.) Poir. near threatened climber 1500−2400
Dryopteridaceae Arachniodes webbiana (A.Braun) Schelpe threatened herb 1380−2600
Dryopteris antarctica (Baker) C.Chr. threatened herb 2500−3320
Ebenaceae Diospyros abyssinica (Hiern) F.White possibly threatened tree 0−2400
Euphorbiaceae Croton alienus Pax threatened shrub or small tree 1525−1825
Euphorbia brevitorta P.R.O.Bally threatened herb 1500−2000
Lamiaceae Plectranthus caespitosus Lukhoba & A.J.Paton possibly threatened herb 1500−2850
Plectranthus punctatus subsp. edulis (Vatke) A.J.Paton threatened herb 1800−3200
Fabaceae Crotalaria agatiflora subsp. engleri (Baker f.) Polhill possibly threatened herb 1500−3500
Crotalaria jacksonii Baker f. threatened shrubs 2200−3000
Lotus corniculatus L. possibly threatened herb 1400−2700
Rhynchosia hirta (Andrews) Meikle & Verdc. Possibly threatened herb 0−1850
Lentibulariaceae Utricularia gibba L threatened herb 10−2550
Malvaceae Hibiscus surattensis L. threatened herb 0−1700
Malva verticillata L. threatened herb 1200−4050
Sparrmannia ricinocarpa (Eckl. & Zeyh.) O.Kuntze threatened shrub 1550−3380
Myrtaceae Eucalyptus globulus subsp. maidenii (F.Müll.) Kirkpatrick threatened tree cultivated
Ophioglossaceae Ophioglossum vulgatum L. possibly threatened herb 1000−3250
Orchidaceae Calanthe sylvatica (Thouars) Lindl. threatened herb 900−3000
Cyrtorchis arcuata (Lindl.) Schltr. possibly threatened epiphyte 0−3300
Habenaria keniensis Summerh. threatened herb 1950−2950
Polystachya caespitifica subsp. latilabris (Summerh.) P.J.Cribb & Podz. threatened herb 1800−2200
Orobanchaceae Phelipanche ramosa (L.) Pomel threatened herb 1735−2250
Passifloraceae Adenia globosa subsp. pseudoglobosa (Verdc.) de Wilde threatened woody climber 0−1850
Pinaceae Pinus radiata D.Don threatened tree 2800−2800
Poaceae Aira caryophyllea L. threatened herb 2000−4500
Andropogon distachyos L. threatened herb 1700−3000
Bromus catharticus Vahl threatened herb 2300−2700
Calamagrostis epigejos (L.) Roth threatened herb 2000−3000
Chloris virgata Sw. threatened herb 10−2120
Lolium temulentum L. threatened herb 1900−2300
Streblochaete longiarista (A.Rich.) Pilg. threatened herb 1500−3280
Polygonaceae Persicaria decipiens (R. Br.) K. L. Wilson threatened herb 1100−1100
Grammitis cryptophlebia (Baker) Copel. threatened epiphyte 1900−2150
Pleopeltis macrocarpa (Bory ex Willd.) Kaulf. possibly threatened herb 1000−3600
Potamogetonaceae Potamogeton pusillus L. threatened herb 600−2000
Pteridaceae Pellaea viridis (Forsk.) Prantl possibly threatened herb 650−2250
Rosaceae Alchemilla fischeri Engl. threatened herb 2320−3440
Prunus africana (Hook.fil.) Kalkm. threatened tree 1350−2750
Rubus keniensis Standl. possibly threatened shrubs 1950−2800
Rubiaceae Galium spurium L. threatened herb 1250−2700
Mussaenda microdonta Wernham threatened shrub or tree 1830−2100
Rubia cordifolia L. threatened climber herb 1140−3120
Rutaceae Toddalia asiatica (L.) Lam. possibly threatened shrub 0−3000
Scrophulariaceae Cycnium tubulosum Engl. threatened herb 130−2400
Smilacaceae Smilax aspera L. threatened shrub 1450−2745
Thelypteridaceae Christella dentata (Forssk.) Brownsey & Jermy possibly threatened herb 45−2200
Stegnogramma pozoi (Lagasca) K.Iwats. threatened herb 2050−3350
Stegnogramma pozoi var. petiolata (Ching) W.A.Sledge threatened herb 2050−3350
Urticaceae Obetia radula (Baker) B.D.Jacks. threatened tree 700−2000
Parietaria debilis G.Forst. possibly threatened herb 1700−4200
Verbenaceae Lantana viburnoides Vahl possibly threatened Woody herb or shrub 0−1950
Xanthorrhoeaceae Aloe nyeriensis Christian threatened shrub 1760−2100

Appendix 2

Endemic species in Aberdare ranges forest

Family Plant species Habit
Acanthaceae Asystasia lorata Ensermu Kelbessa perennial herb
Apiaceae Pimpinella keniensis C. Norman perennial herb
Afrosciadium friesiorum var. bipinnatum (C.C. Towns.) P.J.D. Winter perennial herb
Heracleum taylori C. Norman perennial herb
Apocynaceae Brachystelma keniense Schweinf. perennial herb
Asteraceae Helichrysum formosissimum var. guilelmii (Engl.) Mesfin Tadesse perennial woody herb or shrub
Helichrysum formosissimum Sch.Bip. perennial woody herb or shrub
Senecio aequinoctialis R.E.Fr. perennial woody herb
Asteraceae Helichrysum brownei S. Moore perennial herb or shrublet
Senecio roseiflorus R.E. Fr. perennial woody herb or shrub
Dendrosenecio battiscombei (R.E.Fr. & T.C.E.Fr.) E.B. Knox perennial shrub
Helichrysum chionoides Philipson perennial shrub
Dendrosenecio brassiciformis (R.E.Fr. & T.C.E.Fr.) Mabb. perennial shrub
Dendrosenecio keniensis (Baker f.) Mabb. perennial shrub
Senecio jacksonii S. Moore perennial herb
Dendrosenecio keniodendron (R.E.Fr. & T.C.E.Fr.) B. Nord. perennial shrub
Carduus silvarum R.E.Fr. perennial herb
Senecio amplificatus C. Jeffrey perennial herb
Carduus millefolius R.E. Fr. annual or perennial herb
Helichrysum gloria-dei Chiov. perennial shrub
Senecio margaritae C. Jeffrey perennial shrub
Gynura campanulata C. Jeffrey perennial herb
Brassicaceae Oreophyton falcatum O.E. Schulz perennial herb
Campanulaceae Wahlenbergia pusilla Hochst. ex A. Rich. perennial herb
Lobelia bambuseti R.E.Fr. & T.C.E.Fr. perennial shrub
Wahlenbergia virgata Engl. perennial herb
Lobelia telekii Schweinf. perennial shrub
Lobelia deckenii (Asch.) Hemsl. perennial shrub
Lobelia gregoriana subsp. sattimae (R.E.Fr. & T.C.E.Fr.) E.B. Knox perennial shrub
Caryophyllaceae Uebelinia crassifolia T. C. E. Fries annual herb
Cucurbitaceae Zehneria subcoriaceae Y.D. Zhou & Q.F. Wang perennial herbaceous climber
Cyperaceae Carex runssoroensis var. aberdarensis Kük. perennial herb
Ericaceae Erica silvatica (Engl.) Beentje perennial shrub
Erica filago (Alm & T.C.E.Fr.) Beentje pluriannual shrub
Fabaceae Adenocarpus mannii Hook.f. perennial shrub
Trifolium cryptopodium Steud. ex A. Rich. perennial herb
Crotalaria jacksonii Baker f. annual shrub
Loranthaceae Agelanthus sansibarensis subsp. montanus R. M. Polhill & D. perennial shrub
Lythraceae Nesaea kilimandscharica var. ngongensis B. Verdcourt perennial woody herb or shrub
Malvaceae Abutilon longicuspe var. pilosicalyx Verdc. perennial shrub
Menispermaceae Cissampelos friesiorum Diels perennial herbaceous climber
Moraceae Dorstenia afromontana R. E. Fries annual herb
Passifloraceae Adenia globosa subsp. pseudoglobosa (Verdc.) de Wilde perennial shrubby climber
Poaceae Eragrostis amanda Clayton perennial herb
Primulaceae Embelia keniensis R.E.Fr. pluriannual arboreal
Ranunculaceae Delphinium macrocentrun Oliv. perennial herb
Anemone thomsonii Oliv. perennial herb
Ranunculus aberdaricus Ulbr. perennial herb
Rosaceae Alchemilla johnstonii Oliver perennial shrub
Alchemilla ellenbeckii Engl. perennial herb
Alchemilla cyclophylla T.C.E.Fr. perennial herb
Rubus friesiorum Gust perennial shrub
Alchemilla argyrophylla T.C.E.Fr. perennial shrub
Rubiaceae Galium ruwenzoriense (Cortesi) Ehrend. perennial herb
Pavetta abyssinica var. lamurensis Verdc. pluriannual arboreal
Oldenlandia friesiorum Bremek. perennial herb
Canthium oligocarpum subsp. friesiorum (Robyns) Bridson pluriannual shrub or tree
Galium glaciale var. satimmae Verdc. perennial herb
Scrophulariaceae Bartsia longiflora Hochst. ex Benth. perennial herb
Solanaceae Solanum agnewiorum Voronts. perennial shrub
Xanthorrhoeaceae Aloe nyeriensis Christian perennial shrub
Apiaceae Afrosciadium friesiorum (H. Wolff) Winter perennial herb
Afrosciadium englerianum H. Wolff) P.J.D. Winter perennial herb