Assessing the global conservation status of the rock rose Helianthemum caput-felis
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Assessing the global conservation status of the rock
rose Helianthemum caput-felis
ELENA SULIS, GIANLUIGI BACCHETTA, DONATELLA COGONI
D O M E N I C O G A R G A N O and G I U S E P P E F E N U
Abstract The assessment of the conservation status of a Introduction
species is the first step in developing a conservation strategy.
IUCN Red Lists assessments are an important starting point
for conservation actions and the most commonly applied S pecies face numerous threats, principally related to
human activities, and biodiversity continues to be lost
(Pimm et al., ; Butchart et al., ; Ceballos et al.,
method for assessing the extinction risk of a species. In
this study, the global conservation status of the rock rose ). Halting, or at least significantly reducing, the loss of
Helianthemum caput-felis Boiss. (Cistaceae), a perennial biodiversity requires adequate investment and a compre-
Mediterranean plant, was evaluated using the Red List hensive and reliable measure of conservation status (e.g.
criteria. The distribution of the species was determined by Balmford et al., ; Fenu et al., ; Orsenigo et al.,
monitoring historical localities and all other suitable sites ). Target II of Objective I of the Global Strategy for
along the western Mediterranean coasts for years. For Plant Conservation – of the Convention on
each confirmed locality, the ecological and population para- Biological Diversity (CBD; GSPC, ) is the preliminary
meters and the main threats were recorded; these data were assessment of the conservation status of the Earth’s flora.
used in a quantitative analysis of the species’ extinction risk. Evaluation of species conservation status is required
Our findings indicate there have been several recent extinc- not only to evaluate progress towards the CBD’s Aichi
tions, and there is a continuing decline in the species’ area Targets of the Strategic Plan for Biodiversity –
of occurrence, habitat quality and number of reproductive (Pimm et al., ) but also to identify and develop effect-
plants. The main threats are related to human activities. ive conservation strategies (Rodrigues et al., ; Mace
Extinction models indicate a probability of quasi-extinction et al., ; Fenu et al., a; Rossi et al., ; Collen
risk of c. % in five generations or c. % in three genera- et al., ; Orsenigo et al., ). The IUCN Red List
tions, with the species likely to become extinct in seven cur- criteria (IUCN, , a) are the accepted standard
rently known localities within the next years. Application for assessing the extinction risk of species (Rodrigues
of the Red List criteria indicates H. caput-felis should be ca- et al., ; Mace et al., ; Collen et al., ;
tegorized as Endangered. This study confirms that legal pro- Orsenigo et al., ).
tection and passive conservation measures are insufficient Habitat Directive //EEC is the core strategy for na-
to guarantee the persistence of a plant species. Active con- ture conservation in Europe (Balmford et al., ; Pullin
servation and management actions are needed to protect et al., ; Beresford et al., ; Fenu et al., ).
this and other threatened species of the Mediterranean Through the implementation of cogent conservation pol-
Basin. icies, the Directive promotes the maintenance of a favour-
able conservation status for a group of key species and
Keywords Cistaceae, conservation status, extinction risk, habitats (European Commission, ; Rossi et al., ;
Helianthemum caput-felis, IUCN Red List, Mediterranean Fenu et al., ). It is mandatory for EU member states
flora, rock rose, threatened plant that have full responsibility for their conservation efforts
Supplementary material for this article is available at to monitor and report the conservation status of all species
https://doi.org/./S listed in the Directive (European Commission, ; Rossi
et al., ; Fenu et al., ).
One of the key species listed in the Habitat Directive is
the rock rose Helianthemum caput-felis Boiss. (Cistaceae),
which is protected by several international, national and
regional regulations. Helianthemum caput-felis is a ther-
ELENA SULIS, GIANLUIGI BACCHETTA, DONATELLA COGONI (Corresponding author,
orcid.org/0000-0003-0937-196X) and GIUSEPPE FENU ( orcid.org/0000- mophilous long-lived half shrub that grows in coastal
0003-4762-5043) Dipartimento di Scienze della Vita e dell’Ambiente, Centro environments under the direct influence of the sea, mostly
Conservazione Biodiversità, Università degli Studi di Cagliari, Cagliari, Italy
E-mail d.cogoni@unica.it
on calcareous rocky cliffs with garrigues or scrublands;
some populations grow on sand dunes in Majorca, fossil
DOMENICO GARGANO Dipartimento di Biologia, Ecologia e Scienze della Terra,
Università della Calabria, Arcavacata, Italy dunes in Morocco and rocky slopes bordering inland
Received May . Revision requested August . ravines (Fenu et al., b). The species occurs in several
Accepted November . First published online November . disjunct and fragmented populations throughout the coasts
Oryx, 2020, 54(2), 197–205 © 2019 Fauna & Flora International doi:10.1017/S0030605318001424
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198 E. Sulis et al.
of the western Mediterranean Basin (south-east Iberian size (sensu IUCN, ) was estimated as d × A × p, where
Peninsula, Balearic Islands, Sardinia and north-west Africa; d is an estimate of density within the sampled plots, A is
Fenu et al., b and references therein). The global conser- an estimate of the area occupied by the population, and p
vation status of H. caput-felis was previously unknown is an estimate of the proportion of mature individuals within
because only regional or local assessments were available, the sampled plots. Populations were categorized in three size
and there was little information on the species distribution classes, defined a priori as small (, individuals), me-
and conservation status in Africa. Helianthemum caput-felis dium (–,) and large (. ,). The presence or ab-
is categorized as Endangered in Europe (Bilz et al., ) and sence of seedlings was also recorded in each locality by
Spain (Agulló et al., ), and as Critically Endangered in surveying the population several times during the recruit-
Italy (Fenu et al., b) and Algeria (Agulló et al., ). In ment season. Demographic data were collected on per-
addition, according to the European Habitat Directive manent plots in six populations across the species range
H. caput-felis has an inadequate conservation status in that were representative of the range of ecological conditions
Italy (Fenu et al., ). in which the plant grows (Table ; Sulis et al., ). In each
Here, to help establish a conservation plan for H. caput- population, after excluding areas with marginal conditions
felis, we evaluated the species’ global conservation status for the species, permanent plots ( × m) were placed ran-
using the Red List criteria. We aimed to: () describe the domly in the area where the species was found; within the
species’ range based on extensive field surveys, () quantify plots all plants present (a total of in the plots in the
the size and structure of populations, () identify the main first census) were marked, mapped and monitored over a
threats to the species’ persistence, () assess the species’ -year period.
global conservation status, and () recommend appropriate
conservation measures.
Data analysis
Methods To assess the extinction risk of H. caput-felis we used the
Red List criteria (IUCN, ) and the guidelines for their
Data collection application (IUCN, ), considering the criteria A, B and
E. To determine whether H. caput-felis fulfilled criterion A
The geographical distribution of H. caput-felis was deter- we assessed any potential population reduction (observed,
mined through field surveys during – in all estimated or inferred) in the last years or three genera-
localities for which there were herbarium specimens or tions, based on the area of occupancy (AOO; the area within
database records (Supplementary Table ) and/or published the extent of occurrence occupied by the taxon, see below;
data (Agulló et al., ; Fenu et al., b; Sulis, ). IUCN, ).
Additionally, all sites along the coasts of Sardinia, the To apply criterion B, the extent of occurrence (EOO; the
Balearic Islands and the Mediterranean coasts of Spain and area contained within the shortest continuous imaginary
Morocco with suitable ecological conditions for the species boundary that could be drawn to encompass all known
were surveyed. No surveys were made on the Algerian sites of occurrence of a taxon, excluding cases of vagrancy)
coast, for which information was obtained from Agulló and the AOO were calculated from the distribution records.
et al. (). Extinctions that predated were excluded from these cal-
In each locality where occurrence of the species was con- culations. To estimate EOO, the minimum convex polygon
firmed or discovered, the following analyses were under- that included all the occurrences was drawn (IUCN, ),
taken. The geographical limits of confirmed localities were with unsuitable areas excluded by deriving the correspond-
mapped and their area estimated using ArcGis . (Esri, ent α-hull using the Delauney triangulation (Burgman &
Redlands, USA). Localities separated by . km were con- Fox, ; Gargano et al., ; IUCN, ). The AOO
sidered to be geographically separate. At each locality the was calculated by generating a × km grid with ArcGis.
altitudinal range, slope, aspect and habitat type according To apply criterion E the estimated quasi-extinction risks
to the Habitat Directive were determined. Major threats of populations were calculated based on a demographic
to H. caput-felis were identified through field observations study that used both an integral projection model and a
(except for Algerian localities), and categorized following matrix population model (Sulis, ; Sulis et al., ;
the IUCN Threats Classification Scheme (IUCN, b). Supplementary Material ). The matrix projection model
Where possible, population size was determined by a dir- was used to calculate the estimated quasi-extinction risk
ect count of the total number of mature plants. In extensive using the popbio package (Stubben & Milligan, ) in
localities, population size was estimated from a count of all R .. (R Core Team, ). The mean generation time
individuals in – plots (each plot was m; the number of (T) extracted from the integral projection model was .
plots depended on the location); in these cases population years ( generations = . years) and the mean value
Oryx, 2020, 54(2), 197–205 © 2019 Fauna & Flora International doi:10.1017/S0030605318001424
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TABLE 1 Localities of Helianthemum caput-felis surveyed in this study, with altitudinal range, area, mean density ± SD, population size, whether seedlings were present, protection status,
current status, source and the main threats (IUCN, b). Localities in bold are those selected for study of detailed population dynamics (Sulis et al., ).
Country, Altitudinal Area Mean density ± Population Seedlings Current
No. region Locality (municipality) range (m) (ha) SD (plants/m2) size1 present Protection2 status Source Threats
Italy
1 Sardinia Is Arutas (Cabras) 5–15 0.001 SmallC No None Confirmed This study 4.1, 6.1, 8.1,
9.4
2 Sardinia Su Tingiosu–Porto Suedda 5–25 12.743 4.8 ± 2.42 LargeE Yes None Confirmed This study 2.1; 2.2; 3.2;
(Cabras) 6.1; 8.1; 10.3
3 Sardinia Seu (Cabras) None Extinct This study
4 Sardinia Capo Mannu (San Vero Milis) 5–55 17.868 4.6 ± 2.25 LargeE Yes SCI Confirmed This study 2.1; 2.2; 6.1;
8.1; 10.3
Spain
5 Majorca Punta es Bauç (Santanyí) 8–10 0.012 SmallC No SCI Confirmed This study 6.1
6 Majorca Colònia de Sant Jordi–Playa del 3–8 5.533 1.6 ± 0.74 LargeE No SCI* Confirmed This study 1.1; 1.3; 6.1;
Puerto (Ses Salines) 9.4
7 Majorca Colònia de Sant Jordi–Es Trenc 2–4 0.493 3.0 ± 1.41 LargeE Yes SCI Confirmed This study 6.1
(Ses Salines)
8 Majorca Sa Ràpita–backdune (Campos) 2–10 10.495 7.8 ± 5.57 LargeE Yes SCI Confirmed This study 6.1
9 Majorca Sa Ràpita–nautical club 3–6 0.416 9.6 ± 1.85 LargeE Yes None Confirmed This study 1.1; 2.1; 4.1;
(Campos) 6.1; 8.1
10 Majorca Cap Blanc (Llucmajor) 90–110 101.359 2.5 ± 1.14 LargeE Yes SCI Confirmed This study 4.1; 10.3
11 Majorca Cala Pi (Llucmajor) 15–20 0.120 SmallC No SCI Confirmed This study 1.1; 1.3; 4.1;
6.1
12 Majorca Maioris (Llucmajor) Not This study
retrieved
13 Ibiza Cala Conta (San José) Not This study
retrieved
14 Alicante Cap d’Or (Teulada) 40–50 0.210 SmallC No SCI* Confirmed This study
15 Alicante Cala del Portitxolet (Teulada) 9–14 1.038 1.4 ± 0.86 LargeE No PMR* Confirmed This study 1.1; 1.3; 4.1;
6.1; 8.1
Rock rose Helianthemum caput-felis
16 Alicante L’Andragó–Les Platgetes 6–12 0.166 1.4 ± 0.54 MediumC No None Confirmed This study 1.1; 1.3; 4.1;
(Teulada) 6.1
17 Alicante Cala els Pinets, Cala Lobella, Cala 10–20 2.203 2.9 ± 0.74 LargeE Yes SCI* Confirmed This study 6.1
de l’Advocat (Benissa)
18 Alicante Cala Fustera (Benissa) 7–11 0.182 1.2 ± 0.57 MediumE No SCI, PMR Confirmed This study 1.1; 6.1; 10.3
19 Alicante Cala de les Bassetes (Benissa) 6–20 0.969 2.8 ± 1.04 LargeE Yes SCI, PMR Confirmed This study 1.1; 6.1
20 Alicante La Caleta (Calpe) 6–10 0.129 1.5 ± 0.79 MediumC Yes SCI*, PMR Confirmed This study 1.1
21 Alicante Calpe (Calpe) 5–10 0.084 3.0 ± 1.37 MediumC Yes SCI* Confirmed This study 1.3; 6.1; 8.1
22 Alicante Cabo de Santa Pola (Santa Pola) Extinct Serra et al.
(2000); this
study
199. https://doi.org/10.1017/S0030605318001424
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200
Table 1 (Cont.)
E. Sulis et al.
Country, Altitudinal Area Mean density ± Population Seedlings Current
No. region Locality (municipality) range (m) (ha) SD (plants/m2) size1 present Protection2 status Source Threats
23 Alicante Cabo Cervera (Torrevieja) 5–14 1.676 1.1 ± 0.65 LargeE
No None Confirmed This study 1.1; 1.3; 4.1;
6.1; 8.1; 10.3
24 Alicante Torrevieja (Torrevieja) 2–3 0.039 1.4 ± 0.82 MediumC No None Confirmed This study 1.1; 1.3; 6.1;
8.1; 9.4
25 Alicante Cala Mosca and Punta Prima 2–18 9.723 1.8 ± 0.34 LargeE Yes None Confirmed This study 6.1; 8.1
(Orihuela)
26 Alicante Rambla de las Estacas–Cala de 1–10 0.282 SmallC No SCI* Confirmed This study 1.1; 8.1
las Estacas (Orihuela)
27 Alicante Barranco de la Cala del Capitan 15–20 0.067 SmallC No None Confirmed This study 1.1; 1.3; 2.2;
(Orihuela) 8.1; 9.4
28 Alicante Casa de Los Leoncios (Orihuela) 15–20 0.381 SmallC No SCI* Confirmed This study 1.1; 2.2; 6.1
29 Alicante Cala Mosca–Playa Flamenca 1–9 9.723 2.0 ± 0.50 LargeE Yes PMR* Confirmed This study 1.1; 1.3; 4.1;
(Orihuela) 6.1; 8.1; 10.3
30 Alicante Cabo Roig (Orihuela) 3–7 0.906 3.5 ± 1.67 LargeE No None Confirmed This study 1.1; 1.3; 6.1;
10.3
31 Alicante Punta de la Glea (Orihuela) 5–17 4.179 3.1 ± 3.53 LargeE Yes PMR Confirmed This study 1.1; 1.3; 4.1;
6.1
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32 Alicante Dehesa de Campoamor 5–10 0.117 1.5 ± 0.20 MediumC No None Confirmed This study 1.1; 1.3; 6.1;
(Orihuela) 8.1; 10.3
33 Alicante Mil Palmeras (Pilar de la 3–7 1.178 7.7 ± 1.53 LargeE No None Confirmed This study 1.1; 1.3; 6.1;
Horadada) 8.1
34 Alicante Río Mar (Pilar de la Horadada) 1–5 1.377 3.7 ± 1.53 LargeE No None Confirmed This study 1.1; 1.3; 6.1
35 Nador Barranco del Quemadero 100–110 36.908 2.4 ± 1.56 LargeE Yes SCI Confirmed This study 2.2
(Melilla)
36 Nador Barranco del Nano (Melilla) 85–110 24.630 3.2 ± 1.04 LargeE Yes SCI Confirmed This study
Morocco
37 Nador Near Beni Chiker (Beni Chiker) 130–150 0.082 SmallC No None Confirmed This study 2.2; 3.2; 9.4
38 Nador Taxdirt–Cabo de Tres Forcas 100–210 115.639 3.2 ± 1.56 LargeE Yes None Confirmed This study 2.2; 3.2
(Beni Chiker)
39 Nador Near Beni Sidel (Beni Sidel) 180–200 0.142 SmallC No None Confirmed This study 2.2; 8.1
40 Nador Road to Cap de Trois Fourches 180–220 0.150 1.3 ± 0.70 MediumE Yes None Confirmed This study 4.1; 8.1
(Cap de Trois Fourches)
41 Nador Douar Ighzar-n-Yamrabthan 42–67 0.090 1.5 ± 1.10 MediumE Yes None Confirmed This study
(Douar Ighzar-n-Yamrabthan)
42 Nador Duar Izzemmouren (Ras 40–50 4.211 2.3 ± 1.20 LargeE Yes None Confirmed This study 2.2; 2.3
Kebdana)
43 Nador Ras El Má (Ras Kebdana) 35–52 3.686 2.3 ± 1.01 LargeE No None Confirmed This study 2.2; 9.4
44 Nador Near Hidoun (Hidoun) Not This study
retrieved
45 Nador Târia n Tît (Charrana) 30–52 0.540 SmallC No None Confirmed This studyRock rose Helianthemum caput-felis 201
extracted from the matrix projection model was . years
1.1; 1.3; 2.3;
6.1; 8.1; 9.4
Threats ( generations = . years; Sulis, ). Following the pre-
Determined by counting (superscript C) or estimating (superscript E) the total number of mature plants and categorizing as small (, individuals), medium (–,) or large (. ,) population.
cautionary principle (IUCN, ), the smaller value of gen-
eration length (i.e. . years) was retained. Extinction risk
was calculated considering three alternative assessments (
Agulló et al.
Agulló et al.
Agulló et al.
Agulló et al.
years or three generations, years or five generations, and
years). Quasi-extinction probabilities were calculated
Source
(2017)
(2017)
(2017)
(2017)
by model iterations (van der Meer et al., ).
Matrices were selected at random with replacement (each
matrix had an equal probability of selection; Morris &
Confirmed
Doak, ). A quasi-extinction threshold of individuals
Current
Extinct
Extinct
Extinct
status
was designated a priori, to help minimize the demographic
stochasticity associated with small population size (Morris
& Doak, ).
Protection2
We also modelled three separate scenarios, one for each
None
population size class, to examine extinction risk. We developed
each model using the global stochastic growth rate (λs = ;
SCI, Site of community importance; PMR, Plant micro-reserve sensu Laguna et al. (); *protection only partially covers the population area.
Sulis, ; Sulis et al., ) and the effective population size.
Seedlings
present
Results
We located records of H. caput-felis in localities along the
Population
western Mediterranean coasts, mainly in Spain ( localities,
SmallC
including two in Melilla), followed by Morocco (nine local-
size1
ities), Italy and Algeria (four localities in each country;
Table ). We confirmed the presence of H. caput-felis in
Mean density ±
SD (plants/m2)
localities, of which we verified in the field, and one of
which was documented in Agulló et al. (; no. in
Table ). In two localities on the Balearic Islands (Cala
Conta in Ibiza, Maioris in Majorca) and one in Morocco
(near Hidoun, Nador), field surveys carried out by ourselves
and other researchers failed to locate the species. Following
Area
(ha)
a precautionary approach, we reported the species as ‘not re-
trieved’ in these localities. We were, however, able to con-
firm recent extinctions at two localities in Europe (Santa
Altitudinal
range (m)
Pola in Spain, Seu in Italy) and three localities in Algeria.
75–80
All sites where occurrence was confirmed are in coastal
170
environments, with the exception of one population in
50
90
Morocco that is . km from the coast. The altitudinal
range at which we located the species was – m. In
Cabo Lindlés (Aïn-El-Turk)
Europe, we found the plant below m, whereas in
Aïn-El-Turk (Aïn-El-Turk)
Cap Falcon (Aïn-El-Turk)
North Africa the species occurred in some cases above
Locality (municipality)
Aïn-El-Kerma (Oran)
m. The slope of localities is –°. The area occupied
by the species in each locality was variable, from m at
Is Arutas in Sardinia to and ha at Taxdirt and Cap
Blanc, respectively. Mean plant density was . ± SD .
plants/m, varying from . ± SD . plants/m (Cabo
Cervera, Alicante) to . ± SD . plants/m (Sa Ràpita,
Majorca). Population size ranged from a few mature plants
(Is Arutas, Cabras) to more than tens of thousands (Cap
Table 1 (Cont.)
Country,
No. region
Blanc, Llucmajor). More than half of localities (.%) had
46 Oran
Oran
Oran
Oran
a population size . , mature plants. The population
Algeria
size was # individuals in .% of localities. The popu-
47
48
49
lation structure was mainly characterized by reproductive
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. https://doi.org/10.1017/S0030605318001424202 E. Sulis et al.
FIG. 1 Number of localities subject to
each of the main threats (Table ) to the
rock rose Helianthemum caput-felis
populations; data for Algeria was
obtained from Agulló et al. ().
(i.e. Carpobrotus sp., Agave sp., Acacia sp. and Ricinus com-
munis L.; .%), roads and railroads (.%), wood and
pulp plantations (.%), and the presence of rubbish
(IUCN threat classification ‘garbage and solid waste’;
.%). In .% of localities, all in Europe, avalanches
or landslides appear to threaten the persistence of H. caput-
felis (Fig. , Table ).
According to the generation time extracted from the in-
tegral projection model, there was no extinction risk for
three generations (Fig. ), but there was an extinction prob-
ability of c. % for a five generation period (. years;
Fig. ). Considering the generation time extracted from
the matrix population model, the length of three generations
was . years, which corresponded to a quasi-extinction
risk of c. % (Fig. ).
The quasi-extinction risk models for the three popula-
tion size classes, considering each locality to be isolated,
FIG. 2 Simulated cumulative distribution functions of the showed that seven small populations (, plants) are likely
number of years for populations of H. caput-felis to reach a to become extinct within the next years, small popula-
quasi-extinction threshold of individuals: a, three generations
tions with , individuals had a quasi-risk extinction
(integral projection model); b, five generations (integral
projection model); c, three generations based on generation time probability of % in years, and medium populations
from the matrix population model. The lines are separate had quasi-extinction probabilities of and % in
estimates of the cumulative distribution of extinction and years, respectively. Only large populations (. ,
probabilities based on iterations of population growth over individuals) are not at risk of extinction.
years (see Stubben & Milligan, for further details).
Conservation status assessment
and juvenile plants (. %). Despite repeated surveys in the
recruitment season, we observed seedlings in only .% Considering the mean distance between localities ( km)
of localities, with recruitment absent in all small popula- and the results of the Delauney triangulation, the current
tions and in the .% of medium and large populations EOO of H. caput-felis, including all confirmed localities, is
(Table ). , km (Fig. ), and the AOO is km ( × km
The main threats affecting the persistence of H. caput- cells). Since the extinction of H. caput-felis has been
felis populations are related to human activities (Fig. ), documented in five localities (Table ). However, the reduction
including recreational activities (i.e. disturbance effects in EOO was negligible (.%) because these localities were
posed by recreation; .% of localities), housing and within the convex polygon or close to the edge. However, AOO
urban areas (.%) and tourism and recreation (i.e. habi- decreased by three cells ( km), which gave a decline .%
tat effects of tourism and recreation sites with a substantial since . Such values do not reach the minimum threshold
footprint; .%). Other threats were invasive alien species for threatened taxa under Red List criterion A.
Oryx, 2020, 54(2), 197–205 © 2019 Fauna & Flora International doi:10.1017/S0030605318001424
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. https://doi.org/10.1017/S0030605318001424Rock rose Helianthemum caput-felis 203
our research presented here is the first global assessment of
the range and conservation status of H. caput-felis.
The distribution of H. caput-felis is concentrated in the
westernmost Mediterranean Basin along the eastern
Iberian coasts, reaching its easternmost limit in Su
Tingiosu (Italy), northernmost in Capo Mannu (Italy),
westernmost in Beni Chiker and southernmost in Beni
Sidel (both in Morocco). The status of the species in
North Africa remains unclear, however. In three Algerian
localities where occurrence was documented by recent herb-
arium specimens Agulló et al. () were unable to confirm
presence but did locate the species in a previously undocu-
FIG. 3 Extent of Occurrence (EOO) calculated for H. caput-felis. mented locality. The species’ status also requires clarifica-
tion in Morocco, where we could not confirm presence in
Under Red List criterion B the species distribution has one previously documented locality. Considering that this
‘severe fragmentation’ (sensu IUCN, ). Our quantita- species can grow in locations that may be difficult to explore
tive models indicate c. % of confirmed localities (eight (e.g. vertical coastal cliffs, sandy and fossil dunes, inland
medium and small populations) are below the viability ravines), additional surveys are needed.
threshold and therefore could be prone to extinction, close Our global assessment of H. caput-felis as Endangered is
to the % threshold for ‘severe fragmentation’. The Red List consistent with previous regional assessments (Agulló et al.,
guidelines recommend integrating this evaluation with a , ; Bilz et al., ; Fenu et al., b; Rossi et al.,
species’ biological traits, in particular dispersal ability. A ) based only on distribution data (i.e. criterion B).
population genetic study in the Alicante (the core of the Assessments based on geographical data are the most com-
species range, on the Iberian Peninsula), Melilla (North mon for plants, because distribution data are the easiest to ob-
Africa) and Balearic Islands localities, indicated significant tain. However, our integration of criteria B and E provides a
genetic divergence, which would indicate genetic isolation more complete conservation assessment. In addition, the ab-
and limited gene flow among these populations (Agulló sence of seedling recruitment and the high juvenile mortality
et al., ), suggesting that localities separated by longer rate recorded in several localities were further negative indica-
distances (i.e. those in Algeria and Sardinia) may be func- tors (Sulis, ; Sulis et al., ). The null or limited recruit-
tionally isolated. Taken together, these findings suggest ment rate in some populations could be partially explained
the species is severely fragmented. Helianthemum caput- by the effect of drought during – in eastern Spain
felis could therefore be categorized as Endangered based (García de la Serrana et al., ; Laguna & Ferrer, ).
on Bab(ii, iii, iv, v); i.e. its small AOO (), highly fragmen- A combination of some recent extinction events and the
ted distribution (a) and calculated/observed decline (b) in fact that we were unable to relocate the species at some pre-
AOO (ii), habitat quality (iii), number of localities (iv) viously documented locations indicates that the AOO of H.
and number of mature plants (v). caput-felis is contracting, probably as a result of continuing
Helianthemum caput-felis could also be categorized as loss of habitat quality and reproductive individuals. Habitat
Endangered under criterion E as a result of a quasi-extinction reduction and degradation appear to be mainly a result of
risk probability of c. % in five generations (. years based the expansion of infrastructure, a key element in biodi-
on the integral projection model) and c. % in three genera- versity loss (e.g. Newbold et al., ). In particular, as
tions (. years based on the matrix population model). described for several Mediterranean plant species (e.g.
Fenu et al., ; Ballantyne & Pickering, ; Fois et al.,
Discussion ; Orsenigo et al., ), the main threats to H. caput-felis
are related to the degradation of the species’ habitat from
Although many countries are contracting parties to inter- tourism and recreational activities and the expansion of
national conventions and other international regulations, such housing and urban areas. Both the Spanish (Giménez
as the European Habitat Directive, that encourage monitor- et al., ; Agulló et al., ; Marco et al., , ;
ing and protection of wild flora, global protection remains Zaragozí et al., ) and Algerian (Agulló et al., ) coasts
insufficient, with c. % of known vascular plant species threa- have experienced extensive urban development linked to
tened with extinction (Royal Botanic Gardens, ). Moreover, tourism. We did not find that climate change, although a
the number of global species assessments, as required by the major driver of species extinctions (Gómez et al., ;
targets of the Global Strategy for Plant Conservation and the Fenu et al., ; Orsenigo et al., ), is a threat to H.
CBD, is low, and such assessments particularly challenging caput-felis but this could be because of the difficulty of de-
when a species occurs in several countries. We believe that tecting its effects (Fenu et al., ). However, the long-term
Oryx, 2020, 54(2), 197–205 © 2019 Fauna & Flora International doi:10.1017/S0030605318001424
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. https://doi.org/10.1017/S0030605318001424204 E. Sulis et al.
consequences of climate change, especially drought or ir- A G U L L Ó , J.C., J U A N , A., A LO N S O , M.Á. & C R E S P O , M.B. ()
regular rainfall, need to be considered for coastal plants Helianthemum caput-felis Boiss. In Atlas y Libro Rojo de la Flora
Vascular Amenazada de España. Adenda . Dirección General de
such as H. caput-felis (García de la Serrana et al., ;
Medio Natural y Política Forestal (Ministerio de Medio Ambiente,
Laguna & Ferrer, ). y Medio Rural y Marino)—Sociedad Española de Biología de la
Although several populations of H. caput-felis (c. % of Conservación de Plantas (eds Á. Bañares, G. Blanca, J. Güemes,
all localities and c. .% of those in Europe) are currently J.C. Moreno & S. Ortiz), pp. –. Ministerio de Medio Ambiente,
protected (i.e. within a Site of community importance and/ y Medio Rural y Marino, y Sociedad Española de Biología de la
Conservación de Plantas, Madrid, Spain.
or Plant micro-reserve), our findings nevertheless indicate
A G U L L Ó , J.C., J U A N , A., C R E S P O , M.B., A LO N S O , M.Á. & T E R R O N E S ,
that H. caput-felis faces a substantial risk of extinction A. () An updated report on the distribution and conservation
over the short to medium term in the absence of additional status of the Endangered cat’s head rockrose Helianthemum
management actions. As demonstrated for other species caput-felis (Magnoliopsida: Violales: Cistaceae) in Algeria. Journal
(e.g. Aguilella et al., ; Rossi et al., ; Fenu et al., of Threatened Taxa, , –.
), our data indicate that current legal protection and pas- A G U L L Ó , J.C., J U A N , A., G U I L L Ó , A., A LO N S O , M.Á. & C R E S P O , M.B.
() Genetic diversity and phylogeographical assessment of
sive conservation measures are insufficient to guarantee the Helianthemum caput-felis Boiss. (Cistaceae) based on AFLP
persistence of H. caput-felis. This is contrary to EU legislation, markers. Fitosociologia, , –.
which states that conservation of this species is mandatory B A L L A N T Y N E , M. & P I C K E R I N G , C.M. () Tourism and recreation:
and that member states are responsible for its conservation. a common threat to IUCN red-listed vascular plants in Europe.
Helianthemum caput-felis requires a transnational con- Biodiversity and Conservation, , –.
B A L M F O R D , A., B E N N U N , L., T E N B R I N K , B., C O O P E R , D, C Ô T É , I.M,
servation strategy focusing on protection of each locality
C R A N E , P. et al. () The Convention on Biological Diversity’s
in which it occurs, to avoid further decline or extinctions, target. Science, , –.
habitat restoration in degraded localities, mainly in Spain B E R E S FO R D , A.E., B U C H A N A N , G.M., S A N D E R S O N , F.J., J E F F E R S O N , R.
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Acknowledgements We thank Sergio Sulis, Iván Ramos Torrens C O G O N I , D., F E N U , G., C O N C A S , E. & B AC C H E T TA , G. ()
and Eva Moragues Botey (Servicio de Protección de Especies de la The effectiveness of plant conservation measures: the Dianthus
Consejería de Medio Ambiente, Agricultura y Pesca de las Islas morisianus reintroduction. Oryx, , –.
Baleares), Jaime Güemes (Jardín Botánico Valencia), Manuel Tapia C O L L E N , B., D U LV Y , N.K., G A S T O N , K.J., G Ä R D E N F O R S , U., K E I T H ,
Claro (Guelaya-Ecologistas en Acción Melilla) and Jaime X. Soler for D.A., P U N T , A.E. et al. () Clarifying misconceptions of extinction
their help with fieldwork, and the anonymous reviewers and the Editor risk assessment with the IUCN Red List. Biological Letters , .
for their constructive comments. E U R O P E A N C O M M I S S I O N () Council Directive //EEC of May
on the Conservation of Natural Habitats and of Wild Fauna and
Author contributions Conception, design, drafting text: ES, GF; Flora. The Council of the European Communities, Brussels,
Data collection: GB, DC, GF; data analysis: ES, DC, GD, GF; finalizing Belgium.
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Habitats Directive application in Italy. Biodiversity and
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