The systematics of the broader Podarcis hispanicus complex remain unresolved, and while there is good evidence from multiple genetic markers that P. carbonelli should be considered a valid species there is extensive overlap in the distributions of P. carbonelli and a number of other members of the complex (Speybroeck et al. 2016).

This European endemic species is assessed as Vulnerable (VU B1ab(i,ii,iii,iv,v)) on the basis that this species' extent of occurrence is below 14,000 km², the population is considered to be severely fragmented on a precautionary basis, and there is an inferred continuing decline in both the number of mature individuals and the extent and quality of its habitat, and a projected continuing decline in its area of occupancy and the number of subpopulations resulting from climate change. The isolated subpopulation in Doñana is of particular concern due to its small size, suboptimal environment, and genetic pollution.

This European endemic lizard is restricted to Spain and Portugal. It has a highly fragmentary distribution in Spain in the Peña de Francia and Gata (Salamanca) and in the Doñana National Park, and is found in "large isolated fragments" through the central-north Portuguese mountains south to the Portuguese coast as far as Monte Clérigo (Speybroeck et al. 2016). It occurs more contiguously in Aveiro in central Portugal. In western Portugal it occurs down to sea-level in many fragmented sites, and on the Berlenga Islands and Pessuegueiro Island in Portugal (the latter reported by Sillero 2010), while in central Portugal it occurs in hilly sites above 500 m.

Habitat suitability modelling using the most comprehensive available data suggests that a suitable climate is currently more extensive than the species' known range (Sillero and Carretero 2013). Many of these sites are in coastal areas that have been heavily developed, suggesting that it may have once occurred in this region and has become extinct here relatively recently (Sillero and Carretero 2013). In Spain, it is known from between 0–1,200 m.

The species can be common in suitable habitats. In Aveiro in Portugal densities of 1,500-1,600 individuals/ha were reported by Sá-Sousa (2004). The highest known density (2,000-4,000 individuals/ha) has been recorded on Berlenga Island (Vicente and Barbault 2001). The southern subpopulations are generally very small but it can be abundant in tiny areas (Sá-Sousa 2004).

Many subpopulations are probably in decline, especially in the south of its range. Speybroeck et al. (2016) report that the species appears to have declined significantly in abundance over the preceding decade, which they hypothesise may be linked to increasing aridification. "Unexpected low densities" were recorded at a site near the type locality which was once considered to hold one of the densest subpopulations (Sillero et al. 2012). These authors found 43 individuals in six surveys in 1998, but only 27 across 19 surveys in 2012. The population density at the type locality itself, Laguna de San Marcos, was described as being higher than 300 individuals/ha by Pérez-Mellado (1998), and it was considered to be widespread throughout this area of Salamanca (Sillero et al. 2014). During a survey in Laguna de San Marcos in May 2014 these authors found no individuals of this species in a 2.5-hour survey that recorded 11 other species of amphibians and reptiles; they also failed to locate the species at a nearby site from which the species had previously been recorded. In 2013, two-hour surveys in each of Laguna de San Marcos and Nava de Francia each recorded only a single individual (Sillero et al. 2014). These authors caution that these data are insufficient to conclude the species is truly in decline in this area as data are lacking on natural population fluctuations, but note that it presently appears to be "remarkably rare" in areas in which it was regarded as abundant within the preceding two decades. An assumption that this reflects genuine decline is nonetheless consistent with projections by Sillero and Carretero (2013) that the climate in some montane areas may become unsuitable for this species' persistence by 2020.

It is not fully clear that the population presently qualifies as severely fragmented, but this is assumed here on a precautionary basis given these suggestions that once-viable subpopulations are becoming small or are being lost, as the isolated nature of subpopulations will prevent recolonisation following site losses.

This species is found in habitats that lack rocky areas favoured by the common wall lizard (Speybroeck et al. 2016). Coastal and montane subpopulations exhibit different habitat preferences. Montane subpopulations are found in "slightly disturbed" areas (including road banks, trails, small clearings) often close to waterbodies, of open deciduous forest, mainly of oak trees (Speybroeck et al. 2016).

Coastal subpopulations occur in low shrubs in sand dunes (Speybroeck et al. 2016). Animals typically bask on vegetation, but in coastal areas may make extensive use of boardwalks for both basking and shelter (Speybroeck et al. 2016). It is terrestrial in "moderately moist and cool" microhabitats (Sillero and Carretero 2013, citing Sá-Sousa 2004). In Doñana, aridity has been found to be the most significant factor limiting its distribution and preventing its dispersal inland, and this is likely to be the case in other coastal subpopulations, which are buffered against the impacts of dry climates by moister sea air (Román et al. 2006). It lays one to three egg clutches a year, with one to five eggs in each.

Evidence from distribution models, morphology and ecophysiology suggest that the populations in the subranges (Central System, Viseu-Aveiro, Atlantic Coast and Doñana isolate) are undergoing niche divergence in response to difference ecological conditions; this suggests they should be considered as separate ESUs and MUs (Kaliontzopoulou et al. 2010, Carretero and Sillero 2016, Carretero et al. 2016).

This species' fragmentary distribution is hypothesised to be relictual following range contraction since the last Ice Age, and suggests it may therefore be a cool-adapted species that is especially sensitive to ongoing climate warming (Sillero and Carretero 2013). These authors' environmental niche modelling found that the species is associated with areas characterised by both high humidity and low maximum temperature. Sillero et al. (2012) concluded that climate change was the most likely driver of declines recorded between 1998 and 2012 at a site close to the type locality. Sillero et al. (2014) found that a decrease in precipitation, which declined noticeably starting shortly before 2010, was the main environmental correlate of possible declines at the type locality itself.

Sillero and Carretero (2013) modelled two climate scenarios: a 'business as usual' scenario with increasing human populations (A2A), and one with "a general evolution towards environmental protection and social equity" (B2A). In the business as usual scenario, the complete loss of the species from inland areas by 2080 is projected, but both scenarios project a substantial loss of suitable habitat in montane areas by 2050, and suggest that some of its inland range may have become unsuitable by 2020. Although most coastal isolates are expected to survive in the absence of other threats, it is predicted to become extinct in Doñana (Sillero and Carretero 2013).

Loss of habitat due to touristic developments in the south, and wood plantations (pine) in central Portugal are also serious threats.

Hybridisation with other unrelated Podarcis sp. has been reported; in particular, hybridisation with P. vaucheri has been recorded in the Doñana due to urbanisation and may compromise the genetic identity of the species of this isolated range, despite being inside a National Park (Caeiro-Dias et al.2021; M.A. Carretero pers. comm. October 2022).

There is unlikely to be any substantial use of or trade in this species.

The species is "far from being adequately covered" by protected areas (Sillero and Carretero 2013), and while Doñana enjoys a high level of protection these authors' models suggest that it will become extinct in this area as a result of climate change. In central Portugal and Spain, some subpopulations are in natural parks. In the models produced by Sillero and Carretero (2013) only two of these (Serra de Estrela and Costa Vicentina e Sudeste Alentejano), both in Portugal, will retain suitable climatic conditions in the long term.