We live in an increasingly urban world, with conversion to urban land considered among the most irreversible and fastest growing forms of global land-use change (Chen et al., 2020). This rapid urbanization is associated with strong and novel selection pressuressuch as increased heat and pollution, landscape fragmentation and altered hydrologic regimes (Grimm et al., 2008). The simultaneous expansion of urban areas around the world has long positioned cities as a promising model system in biodiversity science (Dearbor & Kark, 2010); with cities serving as an inadvertent, but widely replicated, global experiment to test species' responses to climate change (Youngsteadt et al., 2014), and more recently a broad suite of evolutionary responses (Johnson & Munshi-South, 2017). Indeed, growing recognition of the strength and ubiquity of urbanization-related pressures has led to remarkable growth of urban evolution research in recent years (Miles et al., 2021). This body of work demonstrates rapid non-adaptive and adaptive evolution across a broad range of taxa, from fragmentation-induced genetic drift in salamanders (Noël et al., 2007), to facilitation of gene flow in urban pigeons (Carlen & Munshi-South, 2020), and adaptive phenotypic evolution in killifish (pollution tolerance; Reid et al., 2016), anoles (morphological shifts to navigate artificial surfaces; Winchell et al., 2020) and Virginia pepperweed (faster growth and higher seed production; Yakub & Tiffin, 2017)-among many other examples (Johnson & Munshi-South, 2017; Miles et al., 2021). Many of these species have substantial ecological significance, leading to increased interest in understanding how evolutionary trait changes may affect ecological processes (i.e. eco-evolutionary feedbacks; De Meester et al., 2019) and consequently influence ecosystem function and services in cities (Alberti et al., 2017; Des Roches et al., 2020). However, attempts to quantify eco-evolutionary