The genus Kalanchoe, mostly indigenous from Madagascar and Tropical Africa, is widely traded for ornamental value. In this study, we provided an updated list of wild and cultivated Kalanchoe taxa in Ecuador; we analyzed the temporal–spatial pattern of their records, and we categorized the invasion status for each taxon and its environment preferences. The records of any taxa belonging to this genus were compiled from an extensive search using various information sources. Our results confirmed the presence of 16 taxa of Kalanchoe in the country. Seven species and a hybrid were detected in the wild. Kalanchoe densiflora, K. laxiflora, K. pinnata, K. tubiflora, and K. ×houghtonii were categorized as invasive. We detected invasive records of some of these plants in protected areas. Almost all taxa had at least one record as cultivated, suggesting that the invasion pathway is ornamental trade. Kalanchoe pinnata individuals in the wild were recorded in the four biogeographic regions of Ecuador, which could be associated with the wide range of precipitations and temperatures in which the species may dwell. Our study highlights the importance of reducing the ornamental value and limiting the use of Kalanchoe taxa with invasive potential in horticulture and promoting, instead, the use of indigenous species.

In this study, we provide a comprehensive and updated inventory of the non-native vascular flora of continental Ecuador and analyze its key biogeographic and ecological attributes to inform biological invasion management. We recorded 486 non-native wild plant taxa, 52% of which are naturalized and 48% casual. This inventory was primarily based on secondary data (published literature, scientific reports, and online databases) and enriched through fieldwork and expert consultations. It includes information on taxonomy, life form, lifespan, origin, first year of record, and spatial-temporal distribution. The most represented families were Poaceae (16%), Asteraceae (10%), and Fabaceae (9%). About 60% of the taxa originated from Asia and/or Africa, and 67% are herbs. The earliest introductions date back to the late 18^th century, with an exponential increase beginning in ca. 1915. Only 13% of the taxa have a minimum residence time exceeding 125 years. The Andes accounted for the highest number of taxa (93%, including taxa shared with other regions). Nearly 80% of the non-native taxa have documented uses, most commonly ornamental (42%) and medicinal (38%). Naturalized taxa tended to have longer residence times and more frequently reported uses than casual ones, suggesting these traits may influence naturalization likelihood. Due to limited systematic sampling across the country, particularly outside the Central Andes, some spatial bias may exist. However, the integration of citizen science-derived data, a methodological innovation in our study, proved to be a promising approach for addressing knowledge gaps and improving detection efforts in regions with limited research capacity. Our findings offer a foundation for advancing the management of biological invasions in Ecuador through early detection, rapid response (EDRR), and species prioritization. Finally, we provide a practical, adaptable and replicable framework, based on citizen science and appropriate statistical analyses, for developing national inventories of non-native plant species in data-deficient countries.

Momordica charantia, una maleza trepadora introducida, es nativa del trópico y subtrópico de Asia y África y se encuentra ampliamente distribuida en Ecuador. En este estudio, examinamos la distribución espacio-temporal de los registros de M. charantia y evaluamos su riesgo de invasión para Ecuador. Se recolectaron ocurrencias de la especie de diversas fuentes (bases de datos y herbarios). Se analizó la distribución de la especie en Ecuador y en áreas prioritarias de conservación, considerando sus preferencias climáticas y ecosistémicas. Se realizó un análisis de riesgo de invasión para Ecuador Continental. Nuestros resultados indicaron que M. charantia fue reportada por primera vez en Ecuador en la región de la costa en 1846. La causa de su introducción es desconocida; sin embargo, una posible vía para su expansión podría estar relacionada con su uso como planta medicinal en Ecuador. Actualmente, la especie está naturalizada en Ecuador y se ha registrado en las cuatro regiones, incluyendo las Islas Galápagos. Se detectó la presencia de la especie en 18 áreas prioritarias de conservación, donde su abundancia parece incipiente y su erradicación factible. La ciencia ciudadana (i.e. iNaturalist) proporcionó la mayoría de los registros de la especie, resaltando su importancia para monitorear especies invasoras. Aunque M. charantia tiene una presencia limitada en ambientes naturales (el 89% de los registros se encuentran en áreas perturbadas), la especie fue categorizada como de “alto riesgo” debido a que en Ecuador hay regiones climáticamente adecuadas para su establecimiento. Además, M. charantia tiene una alta capacidad de dispersión a larga distancia y un considerable potencial para convertirse en maleza en cultivos, representando una amenaza para la agricultura. Destacamos que la presencia de M. charantia en áreas perturbadas podría constituir una fuente de propagación hacia áreas cultivadas, donde la especie podría comportarse como maleza. El manejo de las poblaciones de M. charantia cerca de los cultivos podría mitigar sus posibles impactos agrícolas.

Ecuador, recognized as a megadiverse country, faces growing threats from biological invasions, particularly in the mountainous ecosystems of the Andes. We described patterns of native and non-native plant richness and diversity along an elevational gradient (2,000–4,400 m a.s.l.) on the Tungurahua volcano, testing whether patterns of non-native plant diversity are consistent with directional environmental filtering along the gradient or explained by the effects of residence time, climate-matching, and disturbance intensity. Twenty-five 10 × 2 m transects were established at 100-m elevational intervals following a MIREN-T-adapted protocol. Vegetation cover, abundance, and disturbance were recorded in each plot. A total of 247 taxa were identified, distributed across 75 families and 171 genera. Of these, 180 were native (including 11 endemic), 38 non-native, and the remainder of undetermined origin. Non-native taxa were predominantly herbaceous and originated from Africa, Europe, and Asia. Along the gradient, non-native taxa were concentrated at lower elevations, with narrower elevational ranges and lower maximum elevations than native taxa. Native richness exhibited a mid-elevation peak (~ 3,400 m), whereas non-native richness declined steadily with elevation. Alpha diversity decreased with elevation in both groups, but sharply in non-natives. Beta diversity analyses showed higher turnover among native assemblages, while non-native communities were more homogeneous along the gradient. Overall, these patterns support the directional environmental filtering hypothesis, with climatic constraints limiting the upslope expansion of non-native taxa and weaker evidence for effects of residence time, climate-matching, or disturbance intensity. These findings provide key insights for the management and conservation of tropical mountain ecosystems.

Protected areas (PAs) are central to biodiversity conservation, yet they are increasingly exposed to biological invasions. In continental Ecuador, information on non-native terrestrial spermatophytes in PAs remains scattered across biodiversity platforms, scientific and grey literature, and management documents, limiting broad-scale assessments and management planning. We compiled, validated, and integrated records of non-native terrestrial spermatophytes across 68 continental PAs of the Ecuadorian National System of Protected Areas ( Sistema Nacional de Áreas Protegidas , SNAP its Spanish acronym) using GBIF, iNaturalist, peer-reviewed and grey literature, official management plans, and complementary field observations. Records were taxonomically standardized, curated, and assigned to individual PAs. To explain variation in non-native richness, we evaluated predictors grouped into four categories: PA basic attributes (e.g., extent, year of PA designation), propagule pressure and introduction pathways, anthropogenic disturbance, and abiotic environmental conditions. PA basic attributes (e.g., extent, year of PA designation), propagule pressure and introduction pathways, anthropogenic disturbance, and abiotic environmental conditions. Total non-native taxon richness was modelled using generalized linear models (GLMs). We compiled and validated 3,480 occurrence records, including 2,117 observations from citizen science platforms, 687 herbarium specimens, 371 records from peer-reviewed articles, 123 field observations, 106 thesis records, and 76 inventory records derived from management documents. These records represented 486 non-native taxa from 86 families and 320 genera. Poaceae (55 taxa), Asteraceae (38), and Fabaceae (37) were the richest families, together accounting for approximately 27% of all non-native taxa. Across the full dataset, 204 taxa were recorded only in the wild, 188 only as cultivated, 90 in both conditions, and four remained uncertain in establishment status. Seventeen (25%) PAs had no recorded non-native taxa, whereas Pululahua Geobotanical Reserve and Cayambe-Coca National Park were the richest, with 174 and 172 taxa, respectively. Nearly half of all taxa (47.3%) were recorded in only one PA, while the most widespread taxa, Taraxacum sect. Taraxacum and Trifolium repens , occurred in 17 PAs each. Our dataset included four of the species listed among the world’s worst invasive alien species: Arundo donax , Leucaena leucocephala , Rubus ellipticus , and Spathodea campanulata . The selected GLM identified year of PA designation, extent, distance to the nearest urban area, human density, road density, median human impact, terrain ruggedness, and management type as the main predictors of non-native richness. Richness increased with time since PA designation, extent, road density, median human impact, and terrain ruggedness, while state-managed PAs showed lower expected richness. These results indicate that non-native spermatophytes richness in PA is strongly shaped by propagule pressure, human accessibility, and landscape complexity. Notably, richness increased with time since PA designation, a pattern that contrasts with expectations and may be associated with cumulative introduction history or differences in sampling effort among PAs. This study provides the first integrated national baseline of non-native terrestrial spermatophytes across continental Ecuadorian PAs. By combining heterogeneous data sources into a standardized workflow, it provides a practical foundation for surveillance, early detection, and prioritization of management in a biodiverse yet under-assessed PA network.