Morphological and molecular research by Fitze et al. (2011, 2012) concluded that Psammodromus hispanicus represented a complex of three species. The available name for the eastern lineage is Psammodromus edwarsianus (incorrectly given in some sources as P. edwardsianus), and Fitze et al. (2012) described the western lineage as Psammodromus occidentalis. This arrangement was supported by the findings of Mendes et al. (2017), and accepted by Speybroeck et al. (2020).

This species is endemic to mainland Spain in Europe. It is assessed as Least Concern in view of its wide distribution, presumed large population, and because it is unlikely to be declining fast enough to qualify for listing in a threatened category.

This species is endemic to Europe, where it is restricted to but widespread in the central Spanish Peninsula (Speybroeck et al. 2016). The precise limits between the three species of the Psammodromus hispanicus group remain unclear, as this species exhibits range overlaps with both the eastern and western species (Speybroeck et al. 2016, Faria et al. 2021). Its range can be broadly delimited by Pamplona in the north, Albacete in the south, and Segovia in the west (Fitze 2012). It has been recorded between 660 and 1,350 m asl, but may have a wider elevational range than presently characterised (Fitze et al. 2012).

There is little information on the abundance of this species. Different sampling methodologies have resulted in estimates from as low as two individuals per hectare (using transect surveys that are likely to underestimate abundance - Fitze 2012) to values between 10 and 40 individuals per hectare in subpopulations known to occur at higher than average densities (Fitze 2012). In common with Edwards's Psammodromus, it occupies a narrow successional niche which is likely to result in strong local fluctuations in numbers in non-climax communities as environmental conditions change (Fritze 2012).

This species is found in a region characterised by harsh winters with low temperatures and low precipitation seasonality (Fitze 2012). It favours open microhabitats with patches of bare soil as well as dense, low-lying herbs and shrubs (Fitze 2012). It exhibits a preference for habitats close to human habitation and activity, such as those near cereal fields or degraded habitats, and avoids woodland and other densely-vegetated areas (Fitze 2012).

Females lay three to six eggs per clutch and two clutches may be laid in a year (Speybroeck et al. 2016). The species' lifespan is not much greater than two years (Speybroeck et al. 2016), and many males die after their first reproductive season (Arnold and Ovenden 2002).

This species may be locally threatened by the loss of scrubland to intensive agriculture and fires, and the urbanisation of coastal areas, but overall it is not significantly threatened. Ecological succession tends to result in densely-vegetated habitats unsuitable for this species, which is likely to represent a local impact (Fitze 2012).

There is no information on any use of or trade in this species.

This species is listed on Annex III of the Bern Convention. It is present in many protected areas. Conservation measures should focus on the management of succession processes, together with the protection of bushes and Mediterranean scrub, as closed habitats are unsuitable for this species (Fitze 2012).