## 5 Conclusions  
The study of seric shrubland and marshland ecosystems within the Dofana Biological Reserve provided valuable insights into the dynamics of these environments and an example of the GPP variability of this natural reserve. There were some differences in the rate and extent of decline from maximum to minimum GPP values, reflecting the adaptation of seric shrublands to drought conditions and the vulnerability of marshlands, especially during periods of prolonged drought.  
In seric shrublands, the high heterogeneity in species and vegetation cover/bare soil ratio posed a challenge, leading to a noisy temporal evolution in daily GPP estimates, which is well compensated by monthly aggregates. Despite a general underestimation in the first two years, the WA model improved its performance in 2022, suggesting an improved adaptability to extreme vegetation behavior during accumulated drought.  
In wetlands, both LUE models gave satisfactory results, with a slight underestimation possibly due to low FAPAR values during flooded periods. The ME was in line with expectations for grasslands, while the WA model showed superior performance, with the highest correlation values and low RMSE due to a faster response to drought by the herbaceous species present in this area.  
In general, for both ecosystems and LUE models, higher estimated GPP values result in greater MBE as the underestimation becomes more apparent. Nevertheless, the results of this study suggest that the WA model is a useful tool for estimating GPP in both seric shrubland and marshland ecosystems with a very low and similar NRMSE (0.07 for seric shrubland and 0.06 for marshland), suggesting that the more limiting water is for the plant, the better the model works.  
Conceptualization, P.J.G.-G. and R.D-D.; methodology, P.J.G.-G. and R.D-D.; software, P.J.G.-G., H.N. and D.G.-D.; data curation, P.J.G.-G. and J.C.; writing, review, and editing, P.J.G.-G., J.C., H.N. and R.D.-D.; graphical deployment, P.J.G.-G. and D.G.-D.; supervision, R.D.-D. All authors have read and agreed to the published version of the manuscript.  
This study was funded by MICINN through the European Regional Development Fund [SUMHAL, LIFWATCH-2019-09-CSIC-4, POPE 2014-2020]. The PJG contract is funded by the Spanish Ministry of Science, Innovation and Universities (MICIU) through the research projects SpaFLEXVal (PID2022-137022 OB-C33) and FLEX-S3 (PCI2023-145988-2). Part of this work was also funded by the eLTER Plus project (INFRAIA, Horizon 2020, Agreement no. 871128). [PERSON]'s participation in this study is thanks to the support of the Project ET4 DROUGHT (No. PID2021-127345 OR-C31) funded by the Ministry of Science and Innovation (MICINN-AEI) of Spain and DigiSPAC [TED2021-131237B-C21]. [PERSON] has benefited from \"[PERSON]\" mobility grant (PRX22/00726) funded by the Spanish Ministry of Science, Innovation and Universities (MICIU).  
The raw data supporting the conclusions of this article will be made available by the authors on request.  
Data from EC Towers and complementary sensors were kindly provided by ICTSRBD (Dofana Biological Station, CSIC). The authors are also participants in the CSIC InterdisciplinaryThematic Platforms (PTI) PTI EcoBioDiv and PTI Teledetect and in the thematic network NetOps (RED2022-134438-T) funded by MICIU. This publication has been prepared using European Union's Copernicus Land Monitoring Service information.  
The authors declare no conflicts of interest. The funders had no role in the design of the study; in the collection, analyses, or interpretation of data; in the writing of the manuscript, or in the decision to publish the results.