Aloidendron ramosissimum
(Pillans) Klopper & Gideon F.Sm.
1 photo · Licences CC (Wikimedia Commons / iNaturalist)Click pour agrandir
Pays · région · aire protégée · écorégion · biome
Pas d'interactions documentées pour cette espèce.
Liste rouge IUCN
EN · En dangercritères A4ace↘Décroissante- Évaluation
- 2022 · v3.1
- Altitude
- – m
- Profondeur
- – m
État de la populationTexte officiel évaluation IUCNExpert
The majority of the Richtersveld subpopulations are considered to be in ill-health with between 70% and 100% mortality on foot slopes of mountains due to the extreme nature of the drought that started in 2016 and is still ongoing at the time of assessment. There has been little to no recruitment occurring, even after some areas received relief in the form of over 200 mm of rain (P. van Wyk pers. comm. 2022). Subpopulations that have been observed to have declined severely include the stands on the lower slopes of Hellskloof (69%), Halfmense Pass (97% decline) and Remhoogte (100% decline). Evidence of these declines have been documented on the iNaturalist platform see for example https://www.inaturalist.org/observations/91941966.
Reports from the Spitskop farm locality, northwest of the Richtersveld suggest that there the impacts of the recent drought are not as severe with the adult life stage displaying healthy signs (e.g. flowering and lower desiccation levels) (P. Jacobs pers. comm. 2020). Furthermore, on the upper slopes of the Vandersterrberg mountains in the Southern Richtersveld the subpopulation is still stable.
Based on these observations the overall population is inferred to have declined by between 30 and 40% since 2016. Decline is expected to continue with climate models for the likely emission scenarios where emissions stay at present day levels (RCP 2.6) (Hausfather and Peters 2020) and worst-case scenarios where emissions continue to increase during the 21st century (RCP8.5) indicate that there will be a loss of suitable bioclimatic envelope of between 21% and 99% by the time period 2060 to 2080. Climate models also include new suitable habitat becoming available, an expansion of 50% of suitable habitat under RCP2.6 emission scenario but no new areas are projected under the RCP8.5 scenario. Given the low levels of recruitment from field observations and the fact that heavy browsing pressure from livestock and wildlife is causing significant habitat degradation we suspect that a maximum of 5% of future suitable habitat will be colonized. Future reduction is calculated as =([Negative change cells] - d*[Positive change cells]) / [Present cells], where d* is 5%. Based on this we calculate that under likely emission scenario RCP2.6 the population will decline by a further 19% by 2080.
Reports from the Spitskop farm locality, northwest of the Richtersveld suggest that there the impacts of the recent drought are not as severe with the adult life stage displaying healthy signs (e.g. flowering and lower desiccation levels) (P. Jacobs pers. comm. 2020). Furthermore, on the upper slopes of the Vandersterrberg mountains in the Southern Richtersveld the subpopulation is still stable.
Based on these observations the overall population is inferred to have declined by between 30 and 40% since 2016. Decline is expected to continue with climate models for the likely emission scenarios where emissions stay at present day levels (RCP 2.6) (Hausfather and Peters 2020) and worst-case scenarios where emissions continue to increase during the 21st century (RCP8.5) indicate that there will be a loss of suitable bioclimatic envelope of between 21% and 99% by the time period 2060 to 2080. Climate models also include new suitable habitat becoming available, an expansion of 50% of suitable habitat under RCP2.6 emission scenario but no new areas are projected under the RCP8.5 scenario. Given the low levels of recruitment from field observations and the fact that heavy browsing pressure from livestock and wildlife is causing significant habitat degradation we suspect that a maximum of 5% of future suitable habitat will be colonized. Future reduction is calculated as =([Negative change cells] - d*[Positive change cells]) / [Present cells], where d* is 5%. Based on this we calculate that under likely emission scenario RCP2.6 the population will decline by a further 19% by 2080.
Menaces identifiées(4 menaces classées CMP-IUCN)
2_3_4Scale Unknown/UnrecordedSlow, Significant DeclinesMajority (50-90%)Ongoing5_2_1Intentional use (species is the target)Slow, Significant DeclinesMinority (<50%)Ongoing11_2DroughtsVery Rapid DeclinesMajority (50-90%)Ongoing3_2Mining & quarryingVery Rapid DeclinesMinority (<50%)Ongoing
Description complète des menacesTexte détaillé évaluation IUCNExpert
Due to the species’ slow growth and poor ability to respond to disturbances such as overgrazing or mechanical damage, any disturbance is likely to have a long term effect on the population (Hoffman et al. 2011). Since 2004 there has been ongoing habitat degradation as a result of trampling and overgrazing by livestock in the Richtersveld.
The entire range of this species has been negatively impacted by one of the worst recorded droughts in history for the region. This has reduced the availability of winter precipitation events which the species relies on for recruitment. Furthermore, grazing and browsing availability in the region has been significantly reduced (Michler et al. 2019). This has increased foraging pressure by domestic and indigenous fauna likely leading to the increased mortality of the juvenile age class. Other species of Aloidendron near Rosh Pinah, southern Namibia (Loots and Mannheimer 2003) are negatively impacted by mining and considering the spatial overlap of A. ramosissimum in these areas, this threat is likely impacting this species too. However, the extent and rate to which this is a threat has not been explicitly measured or observed.
Climate models also indicate that there will be ongoing loss of suitable bioclimatic habitat for this species.
Due to the unique growth form of the Aloidendron genus, theft of individuals by horticultural collectors has been recorded, however, this species is not as popular in trade as A. dichotomum and A. pilansii.
The entire range of this species has been negatively impacted by one of the worst recorded droughts in history for the region. This has reduced the availability of winter precipitation events which the species relies on for recruitment. Furthermore, grazing and browsing availability in the region has been significantly reduced (Michler et al. 2019). This has increased foraging pressure by domestic and indigenous fauna likely leading to the increased mortality of the juvenile age class. Other species of Aloidendron near Rosh Pinah, southern Namibia (Loots and Mannheimer 2003) are negatively impacted by mining and considering the spatial overlap of A. ramosissimum in these areas, this threat is likely impacting this species too. However, the extent and rate to which this is a threat has not been explicitly measured or observed.
Climate models also indicate that there will be ongoing loss of suitable bioclimatic habitat for this species.
Due to the unique growth form of the Aloidendron genus, theft of individuals by horticultural collectors has been recorded, however, this species is not as popular in trade as A. dichotomum and A. pilansii.
Habitats préférentiels (classification IUCN)
3_5Shrubland - Subtropical/Tropical Dry★6Rocky areas (eg. inland cliffs, mountain peaks)★
Mesures de conservation recommandéesStratégies de conservation IUCNExpert
The species is listed in CITES Appendix II. Much of its range occurs in the Ais/Richtersveld Transfrontier National Park.
Stress écologiques (5)Stresses Classification — IUCNExpert
1_1Ecosystem conversion1_1Ecosystem conversion1_2Ecosystem degradation2_1Species mortality2_1Species mortality
Usage & commerce (1)Use & Trade — IUCNExpert
13Pets/display animals, horticultureinternationalnational
Priorités de recherche (5)Research Needed Classification — IUCNExpert
1_1Taxonomy1_5Threats1_6Actions3_1Population trends3_4Habitat trends
Niche IUCN globaleRealms · Systems · LMEs · Growth forms · FAOs — biogéographie IUCNExpert
Royaumes biogéographiques
Afrotropical
Systèmes (terrestre/eau douce/marin)
Terrestrial
Formes de croissance
Succulent - tree
Références bibliographiques (10)Sources scientifiques de l'évaluation IUCNExpert
- IUCN. 2022. The IUCN Red List of Threatened Species. Version 2022-1. Available at: <a href="www.iucnredlist.org">www.iucnredlist.org</a>. (Accessed: 21 July 2022).
- Hausfather, Z. and Peters, G.P. 2020. Emissions - the 'business as usual' story is misleading. <i>Nature</i> 577: 618-620.
- Michler, L.M., Treydte, A.C., Hayat, H. and Lemke, S. 2019. Marginalised herders: Social dynamics and natural resource use in the fragile environment of the Richtersveld National Park, South Africa. <i>Environmental Development</i> 29: 29-43.
- Jürgens, N., Schmiedel, U., Haarmeyer, D.H., Dengler, J., Finckh, M., Goetze D., Gröngröft, A., Hahn, K., Koulibaly, A, Luther-Mosebach, J., Muche, G., Oldeland, J., Petersen, A, Porembski, S., Rutherford, M.C., Schmidt, M., Sinsin, B., Strohbach, B.J, Thiombiano, A., Wittig, R. and Zizka, G. 2012. The BIOTA Biodiversity Observatories in Africa—a standardized framework for large-scale environmental monitoring. <i>Environmental Monitoring and Assessment </i> 184: 655-678. DOI: 10.1007/s10661-011-1993-y.
- Cousins, S.R. and Witkowski, E.T.F. 2012. African aloe ecology: a review. <i>Journal of Arid Environments</i> 85: 1-17.
- Van Jaarsveld, E. 2011. The tree Aloes of Southern and Eastern Africa. <i>Cactus and Succulent Journal</i> 83(1): 9-21.
- Hoffman, M.T., Rohde, R.F., Duncan, J. and Kaleme, P. 2011. Repeat photography, climate change, and the long‐term population dynamics of tree aloes in southern Africa. Repeat photography: methods and applications in the natural sciences. In: R.H. Webb, D.E. Boyer and R.M. Turner (eds), <i>Repeat Photography-Methods and Applications in the Natural Sciences</i>, pp. 133-142. Island Press, Washington DC.
- Loots, S. and Mannheimer, C. 2003. The status of <i>Aloe pillansii</i> L. Guthrie (Asphodelaceae) in Namibia. <i>Bradleya</i> 21: 57-62.
- Hilton-Taylor, C. (ed.). 1996. <i>Red Data List of Southern African Plants</i>. Strelitzia 4. National Botanical Institute, Pretoria.
- Bond, W. 1983. Dead leaves and fire survival in southern African tree aloes. <i>Oecologia</i> 58: 110-114.
Évaluateurs & contributeurs (3)Personnes ayant contribué à l'évaluation IUCNExpert
assessor
Raimondo, D., Van Wyk, P.C.V., Jürgens, N., Foden, W., Loots, S., Hoffman, M.T., Eastment, C., Swart, E., Geldenhuys, C., Jacobs, P. & Guo, D.
contributor
Hilton-Taylor, C.
evaluator
Mtshali, H. & Hilton-Taylor, C.
Raimondo, D., Van Wyk, P.C.V., Jürgens, N., Foden, W., Loots, S., Hoffman, M.T., Eastment, C., Swart, E., Geldenhuys, C., Jacobs, P. & Guo, D. 2022. Aloidendron ramosissimum. The IUCN Red List of Threatened Species 2022: e.T31156A110113664. Accessed on 05 May 2026.
Répartition mondiale
Aucune observation géoréférencée avec précision suffisante (<10 km) dans GBIF pour cette espèce.
Consulter sur les bases externes
Observations & statuts
Cartographie
Note nomenclaturale & synonymesDétails taxonomiques + synonymes CoLExpert
Note nomenclaturale
TAXREF v18 — INPN/MNHNSynonymes (3)— redirigent vers cette page
- Aloe dichotoma subsp. ramosissima(Pillans) Zonn.
- Aloe dichotoma var. ramosissima(Pillans) Glen & D.S.Hardy
- Aloe ramosissimaPillans
Sources : Catalogue of Life Cross-References (synonymes) · TAXREF v18 INPN/MNHN (commentaires FR).