**5. Conservation of the priority habitat 5220\***

This is one of the most outstanding ecosystems in Europe, whose extension of presence has been drastically reduced since the mid-twentieth century. Will the European Union be able to preserve this natural heritage? This is a priority habitat since it represents the potential natural vegetation of the territory (the expected state of mature vegetation in the absence of human intervention), that is, as the forests in other rainy territories, the Mediterranean distributions of species such as *G. senegalensis*, *Z. lotus*, and *P. laevigata* subsp. *angustifolia* indicate the maximum vegetation that the exiguous rainfall allows (**Figure 3**).

*Habitats of the World - Biodiversity and Threats*

*QUERCETEA ILICIS* Br.-Bl. ex A. & O. Bolòs 1950

*Pistacio lentisci-Rhamnetalia alaterni* Rivas-Martínez 1975

*Periplocion angustifoliae* Rivas-Martínez 1975

*Rigual & Rivas-M*artínez 1960

*Ziziphetum loti Rivas Goday & Bellot 1944 Gymnosporio europaei-Ziziphetum loti F. Casas 1970*

*Oleo sylvestris-Ceratonion siliquae* Br.-Bl. ex Guinochet & Drouineau 1944 *Asparago acutifolii-Ziziphetum loti* Gianguzzi, Ilardi & Raimondo 1996

*Asparago albi-Rhamnion oleoidis* Rivas Goday ex Rivas-Martínez 1975

*Syntaxonomic scheme of the phytosociological associations that characterize the habitat 5220\*.*

*Calicotomo infestae-Rhoetum tripartitae Bartolo, Brullo et Marcenò 1982*

*Periploco angustifoliae-Euphorbietum dendroidis Brullo, Di Martino & Marcenò 1977*

*Mayteno europaei-Periplocetum angustifoliae Rivas Goday in Rivas Goday, Borja, Esteve, Galiano,* 

rocky or subrupicolous environments.

**Table 2.**

strong slopes and abandoned crops.

with coastal influence.

southeast, in particular, in the area of Sampieri (Ragusa) in contact with formations of the *Crithmo-Limonietea* Molinier 1934 class. The vegetal community *Periploco angustifoliae-Euphorbietum dendroidis* (Sicily and surrounding islands: Pantelleria, Favignana, Levanzo, Marettimo, and Lampedusa [21–24]) characterizes a thermoxerophilous scrub with *P. laevigata* subsp. *angustifolia* and *Euphorbia dendroides* L., of climatic sort, settled in insular coastal environments on volcanic, calcarenite, calcareous, dolomitic substrates, etc. Sometimes, the same formation can also acquire connotations of extra xericity, linked to the stoniness of the substrate in

*Calicotomo intermediae-Maytenetum senegalensis Cabezudo & Pérez Latorre 2001 Oleo sylvestris-Maytenetum europaei* Díez Garretas, Asensi & Rivas-Martínez 2005

In Spain, several communities that are part of the habitat 5220\* also integrate the same alliance (*Periplocion angustifoliae*). The *Ziziphetum loti* association defines a vegetation type composed of intricate spiny shrubs of *Z. lotus* from 1 to 3 m height, among which other species such as *Asparagus albus* and *Ballota hirsuta* (Willd.) Benth. frequently occur, as well as *Ephedra fragilis* Desf. and *Rhamnus lycioides L. subsp*. *oleoides* (L.) Jahand. & Maire more sporadically. The most striking aspect of the community is the mass of thorny branches, in a very apparent zigzag, that interlace with each other forming almost insurmountable barriers. During the winter, *Z. lotus* loses its leaves, while in late spring they turn in a light green shade, so the community has two highly contrasted aspects of physiognomy [9, 10, 16]. The community seems to be well settled in dry riverbeds; however the plains, which are often widely cultivated, are really its optimum. So *Z. lotus* is relegated to very

A similar conservation concern happens in the association *Gimnosporio europaei-*

The community *Mayteno europaei-Periplocetum angustifoliae* represents decidu-

*Ziziphetum loti*, which represents prickly scrubs up to 3 m high, dominated by *G. senegalensis* and usually accompanied by *Z. lotus* [3–5]. This is an endemic plant community of enormous uniqueness and ecological valuableness that is not found in any other part of Europe. Geographically it can be found in the southern area of the province of Almeria (Andalucia), in semiarid thermomediterranean territories

ous by drought shrub formations up to 1.5 m high, dominated by the species *P. laevigata* subsp. *angustifolia* and accompanied by sclerophyllous plants such as *Chamaerops humilis* L., *Pistacia lentiscus* L., *Rhamnus lycioides* subsp. *oleoides*, *Rubia peregrina* L., etc. It is the potential vegetation of the arid inframediterranean strip of southeastern Spain [2, 17, 25, 26]. The abundance of these formations varies from limestone soils where is high, to medium sloped silicate areas where a more open structure is usual, especially in sunny exposures. The dynamic that is related

**16**

#### **Figure 4.**

*Global distance between R. glacialis and G. senegalensis most remote populations and documented distance between them in southern Spain.*

**19**

for this species.

*Intensive Habitat Loss in South Spain: Arborescent Scrubs with* Ziziphus *(5220\*)*

This habitat is so peculiar that in the south of Spain, there are native flora and vegetation communities that range from *G. senegalensis* formations on the coast to alpine communities of *Ranunculus glacialis* L. The latter species, with populations on the Mulhacen summit at 3400 m,, is the vascular plant that reaches the highest northern latitude, while *G. senegalensis* reaches the coasts of South Africa (**Figure 4**). Their Spanish populations are separated by just 30 km in a straight line; and their most remote populations are separated by almost 12,000 km [29, 30].

In addition, the threat level of each species is very important [1, 31–35], but even more so is that of the communities. In fact, European *Z. lotus* habitats are seriously threatened by severe environmental destruction and fragmentation due to several risk factors such as urbanization, infrastructures, as well as agriculture intensifica-

Some studies carried out in the southeastern of the Iberian Peninsula by combined modeling methods of environmental variables, diachronic study based in the historical photointerpretation of the area and fieldwork, showed the strong habitat regression of these communities [36–38]. Only in the province of Almeria (Andalucia, Spain), more than 26,000 ha of potential area have been lost (extension

Reduction in population size, so accentuated in *G. senegalensis* as a consequence of the habitat fragmentation, raises genetic barriers, since the remaining individuals are only a sample of the total number of genes present in the population [39]. Small populations may exhibit an increase in gene drift, inbreeding or outbreeding depression, and a reduction in gene flow [40–43]. The loss of genetic variability as a consequence of habitat fragmentation can have long-term evolutionary consequences and even short-term effects that involve changes at the genetic level that

Genetic structure of plant populations can be determined by a wide range of factors that interact with each other simultaneously. These factors include short- and long-term processes, such as migration, diversification, habitat fragmentation, and selection, that act at local, regional, and global range and that, when interacting with historical factors, determine geographical patterns of genetic diversity [44]. In addition to habitat loss, and due to the decrease in effective size of populations, local risks are increased by the environmental, demographic, and genetic stochasticity. Therefore, genetic variability erodes due to the random loss of alleles because of the effects of genetic drift, decreasing heterozygosity as a consequence

In order to clarify those questions related to the genetic structure of the populations of *G. senegalensis* that could help to establish conservation measures for this species, with the aid of the information generated by Pérez-Salmerón [44], DNA sequences have been used to detect diversity levels, in different localities through species distribution in the Iberian Peninsula (**Table 3**; **Figure 6**). With this information, we will be able to set up the basis for a next design of conservation strategies

Plant material was collected through the distribution of the species in the Iberian Peninsula (10 populations). Once in laboratory, plant material was dried in silica gel and stored at room temperature. To perform the phylogeographic analysis, DNA sequences of the ITS and trnL-trnF plastid regions were amplified from two individuals of each population, according to previous phylogenetic studies performed in *Celastraceae* family [45, 46]. Ribotype and haplotype networks obtained

of presence) for the survival of habitat characteristic species (**Figure 5**).

**6. Genetic study of the species** *G. senegalensis* **in Spain**

alter suitability and viability of the remaining populations.

of the increase of endogamic mating [43].

*DOI: http://dx.doi.org/10.5772/intechopen.85286*

tion and land-use change [36, 38].

*Intensive Habitat Loss in South Spain: Arborescent Scrubs with* Ziziphus *(5220\*) DOI: http://dx.doi.org/10.5772/intechopen.85286*

This habitat is so peculiar that in the south of Spain, there are native flora and vegetation communities that range from *G. senegalensis* formations on the coast to alpine communities of *Ranunculus glacialis* L. The latter species, with populations on the Mulhacen summit at 3400 m,, is the vascular plant that reaches the highest northern latitude, while *G. senegalensis* reaches the coasts of South Africa (**Figure 4**). Their Spanish populations are separated by just 30 km in a straight line; and their most remote populations are separated by almost 12,000 km [29, 30].

In addition, the threat level of each species is very important [1, 31–35], but even more so is that of the communities. In fact, European *Z. lotus* habitats are seriously threatened by severe environmental destruction and fragmentation due to several risk factors such as urbanization, infrastructures, as well as agriculture intensification and land-use change [36, 38].

Some studies carried out in the southeastern of the Iberian Peninsula by combined modeling methods of environmental variables, diachronic study based in the historical photointerpretation of the area and fieldwork, showed the strong habitat regression of these communities [36–38]. Only in the province of Almeria (Andalucia, Spain), more than 26,000 ha of potential area have been lost (extension of presence) for the survival of habitat characteristic species (**Figure 5**).

### **6. Genetic study of the species** *G. senegalensis* **in Spain**

Reduction in population size, so accentuated in *G. senegalensis* as a consequence of the habitat fragmentation, raises genetic barriers, since the remaining individuals are only a sample of the total number of genes present in the population [39]. Small populations may exhibit an increase in gene drift, inbreeding or outbreeding depression, and a reduction in gene flow [40–43]. The loss of genetic variability as a consequence of habitat fragmentation can have long-term evolutionary consequences and even short-term effects that involve changes at the genetic level that alter suitability and viability of the remaining populations.

Genetic structure of plant populations can be determined by a wide range of factors that interact with each other simultaneously. These factors include short- and long-term processes, such as migration, diversification, habitat fragmentation, and selection, that act at local, regional, and global range and that, when interacting with historical factors, determine geographical patterns of genetic diversity [44].

In addition to habitat loss, and due to the decrease in effective size of populations, local risks are increased by the environmental, demographic, and genetic stochasticity. Therefore, genetic variability erodes due to the random loss of alleles because of the effects of genetic drift, decreasing heterozygosity as a consequence of the increase of endogamic mating [43].

In order to clarify those questions related to the genetic structure of the populations of *G. senegalensis* that could help to establish conservation measures for this species, with the aid of the information generated by Pérez-Salmerón [44], DNA sequences have been used to detect diversity levels, in different localities through species distribution in the Iberian Peninsula (**Table 3**; **Figure 6**). With this information, we will be able to set up the basis for a next design of conservation strategies for this species.

Plant material was collected through the distribution of the species in the Iberian Peninsula (10 populations). Once in laboratory, plant material was dried in silica gel and stored at room temperature. To perform the phylogeographic analysis, DNA sequences of the ITS and trnL-trnF plastid regions were amplified from two individuals of each population, according to previous phylogenetic studies performed in *Celastraceae* family [45, 46]. Ribotype and haplotype networks obtained

*Habitats of the World - Biodiversity and Threats*

**18**

**Figure 5.**

**Figure 4.**

*between them in southern Spain.*

*Distribution area of the G. senegalensis plant formations in 1957 and 2011 in Almeria (Spain) [38].*

*Global distance between R. glacialis and G. senegalensis most remote populations and documented distance* 


#### **Table 3.**

*Sampled localities in the work developed by Pérez-Salmerón [44], detailing locality (Loc.), locality code (Cod.), coordinates (Coord.), altitude (Alt.), haplotypes (H), and ribotypes (R).*

**Figure 6.** *Distribution of the sampled localities in the population genetic study of G. senegalensis [44].*

are shown in **Figure 7**. In the case of the ribosomal sequences, among the 20 samples analyzed, it was possible to detect a total of 7 ribotypes (see **Table 3**). The highest distance between ribotypes occurred between R6 and R3, with a distance of six mutational steps. Ribotypes R2, R4, R5, and R6 were found one step away from each other. The most frequent ribotype was R2 (present throughout the distribution of the species, from NAO to MSR), followed by R1 (also of distribution in POR, MSR, and NAO) and R4 (MEL and CAB); the rest of ribotypes were present in a single locality (CAB, EJI, MSR, and NAO). With respect to plastid sequences, it was possible to detect three haplotypes. The most frequent (H2) was present in central and eastern localities (CAB, EJI, MEL, NAO, NER, and POR), whereas the remainder was present in two localities. The highest distance between the most distant haplotypes was four mutational steps.

**21**

**7. Conclusions**

**Figure 7.**

that make them possible.

*Intensive Habitat Loss in South Spain: Arborescent Scrubs with* Ziziphus *(5220\*)*

Ribotype and haplotype networks showed a low intrapopulation genetic diversity, as well as a lack of differentiation among haplotypes according to its geographical distribution. Thus, for example, R2 ribotype is present throughout the distribution of the species (ALQ, MEL, NAO, NER, MSM), while some of the haplotypes were distributed according to their distribution geographic (H1 and H3), and others not (H2). The underrepresentation of haplotypes and ribotypes in the eastern area is in line with the small area and fragmentation of these localities. In order to maintain an in situ representation of the found lineages, it would be necessary to adopt conservation measures in at least half of the sampled popula-

*Ribotype (a) and haplotype (b) networks generated by mean of the maximum parsimony algorithm as implemented in TCS software, by using nuclear (ITS1-5.8S-ITS2) and plastidial (trnL-F) sequences.*

This habitat is seriously threatened. The patches where this type of vegetation can be found are disappearing at a huge rate in Spain, and its presence is very scarce in Italy and Cyprus. For this reason it is consider as priority and fits in the main purpose of the Habitats Directive, which aims not only to conserve species but also entire ecosystems. The philosophy is as simple as powerful: only by protecting the community (biocenosis), all its members will be preserved indefinitely. Nowadays, to conserve implies the protection of the ecosystem, and to achieve this it is necessary to include the ecological processes and the biological components (species)

The lists of "Sites of Community Importance" for the conservation of the Natura 2000 Network, and the designation as "Special Areas of Conservation," have proved to be the most important initiatives for the conservation of the priority habitats. In addition, the elaboration of a checklist of characteristic species is a decisive work for the determination of these sites [47]. The management or restoration measures to ensure the favorable conservation status of the priority habitats are constituted by diverse actions implemented within the framework of LIFE+ program of the European Union (EU), among which can be mentioned, for instance, in Cyprus, the project entitled "Improving the conservation status of the priority habitat types 1520\* and 5220\* at the Rizoelia National Forest Park" (LIFE12 NAT/CY/000758) in which the primary aim has been to promote and enable the long-term conservation of gypsum steppes (*Gypsophiletalia*) and arborescent matorrals with *Ziziphus* in Cyprus, by quantifying and halting natural and anthropogenic pressure and

tions. These populations would be BAÑ, EJI, MEL, MSR, and NAO.

*DOI: http://dx.doi.org/10.5772/intechopen.85286*

*Intensive Habitat Loss in South Spain: Arborescent Scrubs with* Ziziphus *(5220\*) DOI: http://dx.doi.org/10.5772/intechopen.85286*

**Figure 7.**

*Habitats of the World - Biodiversity and Threats*

**Loc. Cod. Coord. Alt. H R** El Alquián ALQ 36°51′N 2°19'W 38 1 2 Baños de Sierra Alhamilla BAÑ 36°57'N 2°24'W 470 1 1 Cabo de Gata CAB 36°44'N 2°11'W 55 2 4 El Ejido EJI 36°45'N 2°48'W 81 2 5 Melicena MEL 36°45'N 3°14'W 17 2 2,4 Rincón de la Victoria MSR 36°42'N 4°19'W 58 3 1,6 Cabo de la Nao NAO 38°44'N 0°13′E 71 2 2,3 Nerja NER 36°45'N 3°50'W 148 2 2 Velilla MSM 36°45'N 3°38'W 116 3 2 Portman POR 37°35'N 0°51'W 58 2 1

*Sampled localities in the work developed by Pérez-Salmerón [44], detailing locality (Loc.), locality code* 

*(Cod.), coordinates (Coord.), altitude (Alt.), haplotypes (H), and ribotypes (R).*

are shown in **Figure 7**. In the case of the ribosomal sequences, among the 20 samples analyzed, it was possible to detect a total of 7 ribotypes (see **Table 3**). The highest distance between ribotypes occurred between R6 and R3, with a distance of six mutational steps. Ribotypes R2, R4, R5, and R6 were found one step away from each other. The most frequent ribotype was R2 (present throughout the distribution of the species, from NAO to MSR), followed by R1 (also of distribution in POR, MSR, and NAO) and R4 (MEL and CAB); the rest of ribotypes were present in a single locality (CAB, EJI, MSR, and NAO). With respect to plastid sequences, it was possible to detect three haplotypes. The most frequent (H2) was present in central and eastern localities (CAB, EJI, MEL, NAO, NER, and POR), whereas the remainder was present in two localities. The highest distance between the most distant

*Distribution of the sampled localities in the population genetic study of G. senegalensis [44].*

**20**

**Figure 6.**

**Table 3.**

haplotypes was four mutational steps.

*Ribotype (a) and haplotype (b) networks generated by mean of the maximum parsimony algorithm as implemented in TCS software, by using nuclear (ITS1-5.8S-ITS2) and plastidial (trnL-F) sequences.*

Ribotype and haplotype networks showed a low intrapopulation genetic diversity, as well as a lack of differentiation among haplotypes according to its geographical distribution. Thus, for example, R2 ribotype is present throughout the distribution of the species (ALQ, MEL, NAO, NER, MSM), while some of the haplotypes were distributed according to their distribution geographic (H1 and H3), and others not (H2). The underrepresentation of haplotypes and ribotypes in the eastern area is in line with the small area and fragmentation of these localities.

In order to maintain an in situ representation of the found lineages, it would be necessary to adopt conservation measures in at least half of the sampled populations. These populations would be BAÑ, EJI, MEL, MSR, and NAO.
