Narcisse bulbocode

Despite the diverse taxonomic rearrangements that this species has gone through precludes an accurate quantification of its subpopulations and the specific threats that they may be impacting them, it is inferred that the identified threats are unlikely to cause the species’ populations to severely decline in the near future.

The abandonment of the traditional ecosystem management practices is the main threat to this species in a short-medium term due to the positive effect of extensive practices, such as grazing, in maintaining or increasing the population size of this species (Ríos et al. 2010). Intensive land management practices (e.g. intensive grazing, the use of herbicides, forest plantations and land ploughing) also represents a negative impact for several natural subpopulations of this species which are now occurring in road edges as a result of changes in these land management (Palacios et al. 2010).

Since these species are related to high moisture soils, changes in rainfall distribution, drought and desertification are a potential threat in the long term. Alegría et al. (2011) predicted an advancement of about eight days in the flowering time for each 1ºC increase in temperature in the Portuguese territory. This phenomenon might change the ecological relationships of this species along the Mediterranean, for instance with pollinators, and subsequently might have consequences on its own abundance and distribution in a near future. 

The increasing interests on the galanthamine-related alkaloid content of the Amaryllidaceae for pharmaceutical purposes (Berkov et al. 2014, Hanks 2002) would represent a threat in the near future, since plants from natural habitats remain an important source of these bioactive substances for the pharmaceutical industry (Berkov et al. 2011). 

Invasive species could negatively impact subpopulations´ survival due to a risk of substitution by presumed natural hybrids occurring within the species´ range. However, the validity of these hybrids has not been confirmed using molecular tools yet.

This species is included in the Annex V of the Habitats Directive (CEE 1992) and therefore its harvesting in the wild is subjected to management regulations. At European level, the plant is listed as Least Concern (Bilz et al. 2011). It is not subject of protection at national level in Spain, Portugal or France. However, it is considered of ‘Special Interest’ at regional level in Extremadura, and as ‘Protected Species not Catalogued’ in Valencia (Palacios et al. 2010). It is also legally protected in Malta under the Schedule VII for Animal and Plant Species of Community Interest whose taking in the wild and exploitation may be subjected to management measures (MEPA 2009). 

In Spain, some populations are present in protected areas such as Doñana, Cabañeros and Monfragüe national parks (IUCN and UNEP-WCMC 2017). In Portugal, it occurs in Serra Amarela in the Peneda-Gerês National Park, outside of the Mediterranean region.

The species is subject to several ex situ conservation strategies, including storage of seed samples for medium-long term conservation in the genebanks of Torretes Botanical Garden, Research Institute CIBIO-University of Alicante, Alcalá de Henares Botanical Garden in Spain, and Museu Nacional de História Nacional-Jardim Botânico, Universidade de Lisboa in Portugal. Thompson (1977) germination experiments might be the starting point to develop germination protocols in genebanks. Moreover, Santos et al. (1998) developed a high productive protocol for bulb micropropagation and, following this procedure, Juan-Vicedo et al. (2015) obtained a stock of in vitro cultures with good rates of multiplication, and a satisfactory rooting and acclimatization which can be used in plant reintroduction programs. Ongoing conservation strategies include living plant collections in the Torretes Botanical Garden and Botanical Garden of Castilla-La Mancha, Spain.

Confirmation of the taxonomic status of this species and related infrataxa is required.