## 1 Introduction  
Extreme-weather-related episodic events are becoming more frequent as a consequence of global climate change [1]. Meteorological extremes can be defined as those occasions when temperature (e.g., heat waves or cold spells), precipitation (e.g., floods or droughs) and/or wind speeds (e.g., hurricanes) break long-term records for a specific site with values well above (or below) a threshold of the studied variable [2, 3]. Climate change, in turn, has been shown to influence lake thermal dynamics by altering lake mixing regimes [4]. In addition, weather-related episodic events facilitate the export of dissolved and particulate compounds from the surrounding terrestrial ecosystems [5]. As a consequence, lake ecosystems are excellent sentinels of change as they respond directly to meteorological episodic events, incorporating the catchment effects and integrating responses over time at different trophic levels [6]. However, responses to climate change in lake ecosystems operate on various temporal scales, and disentangling driver-response relationships impacting freshwater aquatic ecosystems is complex [7]. For this reason, understanding the responses of single climatic forcing events in the context of longer-term dynamics (e.g., seasonal patterns) is important and requires ecological variablesat shorter critical time windows to be explored. In particular, this allows organism response to these disruptive events to be captured [8]. The timing of short or long-term responses differs depending on the variable of interest, from minutes when observing physico-chemical parameters to months or years when studying planktonic communities or higher trophic levels such as fish. High-frequency monitoring allows a more accurate exploration of both the meteorological drivers and their immunological consequences [9], in particular physico-chemical variables such as water temperature and dissolved oxygen (DO) [5]. In contrast, investigations of nutrient and biological responses require analytical and collection time with few studies of episodic events integrating the impact on physical, chemical and biological dynamics [10]. Dystrophic lakes are categorised by low nutrient concentrations (total nitrogen, TN \(<\) 350 \(\mu\)g N\(\cdot\)L\({}^{-1}\) and total phosphorus, TP \(<\) 10 \(\mu\)g P\(\cdot\)L\({}^{-1}\)) [11] and high concentrations of humic matter, which gives a typical brown colour to the water (colour \(>\) 50 mg Pt\(\cdot\)L\({}^{-1}\)) [12]. Humic matter generally originates from terrestrial ecosystems and is directly related to dissolved organic carbon (DOC) concentrations (DOC \(>\) 6 mg C\(\cdot\)L\({}^{-1}\)) [13]. The characteristic brown colour of dystrophic lakes increases attenuation of solar radiation, which has been associated with a reduction of primary productivity [14]. Therefore, dystrophic lakes are characterised as low-productive systems with chlorophyll \(a\) (Chl \(a\)) concentrations of less than 3.5 \(\mu\)g Chl \(a\)\(\cdot\)L\({}^{-1}\)[11]. Terrestrial carbon input tends to promote higher bacterial production and, as such, dystrophic lakes are net heterotrophic systems [15]. In turn, this has an effect on primary consumers by altering food web efficiencies [16]. These types of lakes are commonly found in peatland catchments in northern regions worldwide [17] and particularly in Finland, Sweden, Estonia, the United Kingdom and Ireland [18]. Increasing inputs of terrestrial DOC have been recorded in temperate systems linked to rising temperatures and changes in precipitation patterns due to climate change [6]. However, the complexity of trophic interactions increases the level of uncertainty regarding how these systems are affected by such climatic events, due to observed local differences and synergistic or opposite effects between stressors [6]. In turn, in-lake nutrients and loadings, especially the ratio of nitrogen (N) to phosphorus (P), are important in structuring freshwater planktonic communities.