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# Strong and recurring seasonality revealed within stream diatom assemblages

## Abstract

Improving stream water quality in agricultural landscapes is an ecological priority and a legislative duty for many governments. Ecosystem health can be effectively characterised by organisms sensitive to water quality changes such as diatoms, single-celled algae that are a ubiquitous component of stream benthos. Diatoms respond within daily timescales to variables including light, temperature, nutrient availability and flow conditions that result from weather and land use characteristics. However, little consideration has been given to the ecological dynamics of diatoms through repeated seasonal cycles when assessing trajectories of stream function, even in catchments actively managed to reduce human pressures. Here, six years of monthly diatom samples from three independent streams, each receiving differing levels of diffuse agricultural pollution, reveal robust and repeated seasonal variation. Predicted seasonal changes in climate-related variables and anticipated ecological impacts must be fully captured in future ecological and water quality assessments, if the apparent resistance of stream ecosystems to pollution mitigation measures is to be better understood.

## Introduction

In the context of a changing climate and agricultural intensification, it is recognised that freshwater ecosystems are vulnerable to multiple anthropogenic stressors, including excess sediment and nutrient delivery, whilst also being modulated by climate-dependent flow, water temperature and event-driven transfers from catchments1,2,3. Low-order streams comprise the headwaters of river networks and drain a significant proportion of the UK’s agricultural land. Such streams are central to the functioning of all river networks, forming important corridors linking terrestrial and aquatic ecosystems. These reaches are especially vulnerable to stress as their small channel size relative to catchment area makes them poorly buffered to changes in external climatic, physicochemical and energetic factors4,5,6. However, low-order streams play an important role in regulating downstream processes and, ultimately, the quality of coastal or other receiving waters7,8.

Ecosystem health is assessed using ecological surveys of stream benthos to identify anthropogenic impacts and trajectories of change9,10,11. Within Europe, biological monitoring has been formalised through the Water Framework Directive (WFD)12. This legislation requires an assessment of ecological health, reported as an Ecological Quality Ratio (EQR) which represents the value of an observed biological parameter to that expected under minimally-impaired conditions characteristic of the waterbody type under consideration13. The EQR can vary between values indicative of ‘high’ to ‘bad’ status, with intermediate values indicative of ‘good’, ‘moderate’ or ‘poor’ status. The EQR is based on specific groups of organisms, including macrophytes, fish, macroinvertebrates and diatoms, and informs subsequent development of restorative measures to reduce significant anthropogenic pressures. Full consideration of organism colonisation, resilience to high-energy events and seasonal controls is needed to produce robust biological datasets that capture ecosystem function and variability. Failure to consider this temporal dynamic could bias inferences drawn from ecological assessment and contribute to poorly-targeted mitigation within catchments, potentially incurring significant economic cost.

The incorporation of weather-related factors within monitoring programmes, such as solar radiation, temperature and rainfall that are descriptive of multi-annual seasonal trends, is critical because future climate scenarios are anticipated to have both direct impacts on stream ecosystems and indirect effects mediated via wider catchment processes. For example, the export of phosphorus (P) from agricultural land to waterbodies is predicted to increase in the future, independent of land use change14. Moreover, climate scenarios emphasise an acute increase in the extremes of seasonal cycles with warmer, wetter, winters and hotter, drier, summers in parts of NW Europe15. However, the relative contribution of weather, catchment land use and reach-scale processes on benthic stream ecology has not been rigorously assessed to date via multi-annual, high-resolution in situ environmental monitoring programmes. This is particularly true within highly dynamic low-order streams. We hypothesise that robust and recurrent seasonal controls on stream ecosystems could overwhelm, or at least partially mask, efforts to reduce the effects of anthropogenic stress on streams. Here we present six full years of monthly diatom data from three separate intensively instrumented tributaries of the River Eden, NW England. For the first time, these data enable us to evaluate the resilience and recurrence of seasonal patterns in benthic diatom assemblages. These diatom data are evaluated alongside high-resolution environmental monitoring data to determine the relative discrete and combined contributions of land use, the seasonality of precipitation, temperature and light, and in-stream environmental variables that combine to define the niche experienced by benthic diatoms.

## Results

Distinct and recurring summer and winter diatom assemblages and EQR values are revealed in the monthly data from all three sub-catchments (Fig. 1.3). The greatest range in ecological status was observed within Newby Beck where EQR values varied between those indicative of ‘high’ to ‘bad’ water quality. In contrast, within Thackthwaite Beck which is subject to the lowest intensity of agricultural production, EQR values cycled within the ‘high’ to ‘good’ status classes through all seasons. In all three sites, the EQR indicates much better water quality in spring/summer compared to autumn/winter (Fig. 1.3a–c). Strong stability of diatom assemblages within Pow Beck (Fig. 1.3a) and Newby Beck (Fig. 1.3b) is evidenced through the dominance, in terms of relative abundance determined via valve counts, of two key species; Achnanthidium minutissimum and Amphora pediculus. Periods of improved water quality, as determined by the EQR, are associated with an increase in the ratio of A. minutissimum to A. pediculus, a pattern that is repeated through all six annual cycles. A. minutissimum is a small non-colonial pioneer species (length 15 µm, width 3.5 µm)16, which colonises and reproduces rapidly17 and is often abundant under low phosphorus availability18. A. pediculus, while also a small pioneer species adapted to dynamic discharge conditions (length 11.5 µm, width 3 µm)16, favours environments in which nutrient availability is enhanced19. At Thackthwaite Beck, the least impacted of the three sites in terms of nutrient enrichment, A. minutissimum dominated throughout each year and increased in relative abundance during spring and summer. At this site A. minutissimum was almost seven times more abundant than the next two most abundant species; Gomphonema parvulum and Navicula lanceolata. Nevertheless, these latter two species also display repeated seasonal patterns throughout the time series, with the motile guild species N. lanceolata increasing in dominance under autumn/winter conditions (Fig. 1c) suggesting that higher current velocities and nutrient concentrations could be behind this temporal pattern. The dominance of pioneer species across our dataset suggests that these diatom assemblages are kept in a dynamic equilibrium state throughout the annual cycle. Further functional responses are found in Thackthwaite Beck, where repeated switching in dominance between G. parvulum and N. lanceolata represents the temporal interaction between a high-profile, larger species characteristic of nutrient enrichment (G. parvulum), and species indicative of the motile guild that are better adapted to high flow-low nutrient availability conditions (N. lanceolate). Although different species composition was found between the three independent streams, the same co-aligned seasonal pattern of species change was observed.

Environmental controls on species composition were investigated using a 5-year subset of data from Newby Beck, comprising the most complete flow and water chemistry data (Fig. 2a). These high frequency in situ measurements reveal a strong relationship between weather-related variables (including rainfall, radiation and temperature), discharge conditions, and nutrient and sediment concentrations14,20. The cyclical nature of the monthly diatom data is strongly supported by ASDHR results (Arbitrary Sampled Dynamic Harmonic Regression; Fig. 2b, showing the data against the model with its 95% confidence band). This method allows estimation of periodic or seasonal signal components in irregularly-sampled time-series data, providing both an estimate of the periodic components themselves as well as their uncertainty estimates (see Methods). The model explained 82% of data variance (R2 = 0.82) in the EQR metric and the ANOVA F-test was significant at p = 5.2 ∙ 10−10.

Diatom assemblages typically develop over 1–3 weeks20, so the mean value of environmental variables (water temperature, net radiation, nitrate-N, dissolved oxygen, pH, rainfall, turbidity, discharge, total reactive phosphorus and conductivity) for the 21 days prior to diatom sampling were used to explore species-environment interactions. Spring and summer diatom samples scored highly against Principal Component Analysis (PCA) axis 1 with an eigenvalue of 0.2, demonstrating the primary importance of light. These samples were characterised by the presence of Gomphonema olivaceum and A. minutissimum. G. olivaceum is a high-profile guild species indicating resource-unlimited but disturbance-stress conditions, while A. minutissimum, the dominant species in terms of relative abundance as determined by cell counts, is a low-profile guild species that is comparatively resistant to physical disturbance. Under spring/summer conditions, water temperature and net radiation, dissolved oxygen and nitrogen (N) availability are key drivers of the diatom assemblage composition. Variability in spring/summer conditions was indicated through low-profile (Meridion circulare, Rhoicosphenia abbreviata), high-profile (Encyonema minutum) and motile (Surirella crumena) guild species. In contrast, the PCA demonstrates that winter and autumn diatom samples are associated with in-stream conditions, primarily turbidity and discharge, precipitation-related climate variations and phosphorus resource availability, which all plot in the lower left quadrant of Fig. 3. The percentage of A. minutissimum is inversely related to A. pediculus, the dominant pioneer species under rainfall-driven discharge-phosphorus winter conditions14. The presence of low-profile (Cocconeis euglypta) and motile (Navicula cryptotenella and Caloneis bacillum) guild species along with A. pediculus indicates the importance of variables occurring under winter conditions. Seasonality and nutrient resource availability are important in determining contrasting summer and winter ecological states, with instream variables of conductivity, water temperature and pH switching in relative importance as drivers of diatom assemblage composition between seasons.

## Discussion

These three independent and contrasting sub-catchments of the River Eden, characterised by different levels of agricultural intensity, demonstrate robust and recurring seasonal patterns in stream benthic diatom assemblages over a six-year period. The resilience of the assemblage at this seasonal scale is greater than shown previously21,22 offering species-environment insights for catchment management programmes. Moreover, intensive instrumentation in these catchments has allowed antecedent environmental conditions occurring during biofilm formation to be captured20. Our study demonstrates the crucial temporal perspective that is required to understand ecosystem variability, function and response to seasonality at inter- and intra-annual scales. The long-term diatom time-series displays a dynamic community of pioneer species, implying a constant resetting of the benthic community constrained within characteristic seasonal equilibria. The diatom taxa reflect the impact of both nutrient and stream conditions with a seasonal signature emerging through changes in relative species abundance. Changes in these underlying drivers, both anthropogenic (e.g. discharge associated changes in phosphorus concentration) and weather-related (water temperature, net radiation, and rainfall), combine to shift the ecosystem into clearly-defined alternative states under winter and summer conditions. Community variation left unexplained in the analysis can potentially be attributed to variables not measured in this study, including the influence of grazing23. To increase our ability to predict ecological responses to changes in regional weather and climate patterns, it is necessary for future studies to integrate long-term, empirical survey data with models and manipulative experiments.

Multiple seasonal trends at regional scale provide a dynamic baseline against which land-use decisions are made, and this baseline itself is expected to change in the future. For example, projections for the study catchment region suggest a rise in mean annual temperature between 2.5 °C to 3.3 °C by the 2070 s under a ‘medium’ emissions scenario. The anticipated outcome is that more intense seasonal changes will be observed in rainfall, with drier summer and wetter winter conditions expected15. Across seasonal and multi-annual scales, direct weather variables (temperature, light) are the dominant factors dictating diatom assemblage, with seasonally-delivered nutrients providing further temporally-mediated regulation of diatom assemblages. An important consequence is that future climate changes could undermine catchment remediation programmes whose ‘success’ is typically measured over the short-term. Furthermore, current ecological monitoring frameworks are based largely on detecting responses to organic pollution under spring and autumn conditions. These programmes give little consideration to seasonal characteristics of diatom assemblages and will not capture this shifting seasonal baseline, nor how the health of a stream ecosystem over a full annual cycle may respond to land management strategies. Given climate predictions and suggested requirements for agricultural land-use change to mitigate phosphorus export24, current assessments of ‘ecological status’ will increasingly become obsolete over time, as the baseline drifts to new warmer and wetter conditions. The different components of seasonal change (e.g. temperature, hydrology and atmospheric composition) not only affect multiple levels of biological organisation, but may also interact with other facets of anthropogenic stress to which rivers are exposed25,26,27. It is critical that future research addresses these potentially important synergies underpinned by a clear understanding of climate forcing and trajectories. Given the evidence presented here showing a strong and recurring seasonality in benthic diatoms in stream ecosystems, understanding future ecological variability is important to inform current and future conservation strategies. Capturing this dynamic will ensure that ecological function is maintained across all seasons, as well as allowing for better predictive models of how freshwater systems may respond to management under increasingly contrasting seasonal conditions.

## Methods

### Description of study sites

This study presents data for three low-order streams (Fig. 1 (1.1)); Newby Beck (Strahler second order: OSGB NY-59957,21249) which drains 12.5 km2 of the headwaters of the Morland catchment, Pow Beck (Strahler third order: OSBG NY-38685,50074) which drains an area of 10.5 km2 and Thackthwaite Beck (Strahler second order: OSBG NY-41190-25320) which drains 10.2 km2 of the headwaters of the Dacre Beck catchment, within the larger River Eden catchment, NW England. The three sub-catchments form part of the River Eden UK Demonstration Test Catchment (DTC) programme, a catchment-scale research platform funded by the Department for the Environment, Food and Rural Affairs (2009–2018). Differences in bedrock, superficial geology, land use, rainfall and water quality characteristics are found among the three sub-catchments28. Briefly, Pow Beck, with sandstone bedrock, supports intensive agricultural land use practice giving rise to higher diffuse N and P pressures within the catchment. Thackthwaite Beck, lying on hard rock of volcanic andesite sheets, is a flashy, oligotrophic, upland catchment. Newby Beck drains exposed steeply dipping, fractured carboniferous limestone, shale and sandstone units. Having improved grassland, with rough grazing and arable land as the predominant land use, Newby Beck is exposed to intermediate diffuse pollution pressures in comparison to the Pow Beck and Thackthwaite Beck catchments. All three catchments have a superficial layer of post-glacial till, separating much of the surface hydrological response from the direct influence of the bedrock geology.

### Diatom preparation and identification

Diatoms were collected mid-monthly from March 2011 until August 2016 for all three streams. On each sampling occasion, five representative submerged cobbles were selected from typical riffle areas. Cobbles were scraped with a hard bristle brush and the diatom suspension collected. Samples were processed using 30% hydrogen peroxide and permanent slides were prepared using Naphrax29. 300 valves were identified30,31,32,33,34,35 by the same analyst accredited within the UK Diatom Quality Assurance Scheme36. Calculation of EQR was undertaken using DARLEQ II software. More details are given in Supplementary Information.

### In situ environmental monitoring

Automatic weather stations installed in each catchment measured precipitation, air temperature, relative humidity and net solar radiation at 15 minute intervals28. A weather station centrally located between the three catchments produced total sunshine hours (Penrith Weather Station, 2017). In situ environmental and ecological monitoring occurred at catchment outflows (Fig. 1 (1.1)). Bank-side monitoring stations adjacent to biological sampling areas provided in situ water quality measurements at a minimum resolution of 15 minutes. Hach Lange nutrient analysers provided total reactive phosphorus (TRP) and nitrate (NO3-N) concentration data. Dissolved oxygen (electrochemical sensor, 0–500% ± 2%), pH (0–14 units ± 0.2 units), temperature (−5 to + 50 °C ± 0.15 °C), turbidity (0–1000 NTU, ±2% of reading or 0.3 NTU) and conductivity (0–100 µS cm−1 ± 0.5%) were analysed every 15 minutes using an YSI 6600 sonde. Discharge calculations were made by applying a stage-discharge relationship to 15 minute water level readings recorded by a pressure transducer. The stage-discharge relationship was developed through the collection of manual current metering measurements, and extrapolated beyond the gauged range using standard assumptions for the stage-discharge relationship and the hydrological water balance37. The in situ analysis was quality assured using monthly laboratory analysed samples to ensure accuracy in the measurements.

### Data analysis

PCA was used to determine the importance of environmental controls on the benthic diatom assemblages. PCA relates species composition to measured environmental gradients by reducing the dimensionality of complex, multivariate data, finding a small number of linear combinations of variables which are visualized using an ordination diagram38. All water chemistry data used within this analysis was averaged over the preceding 21 days to account for diatom community colonisation processes20. Values of turbidity, rainfall and discharge along with the species matrix were Log-transformed (Ax + B). All ordinations were performed using CANOCO version 5.1 software39.

Time-varying seasonal analysis (Mindham and Tych, 2018 in submission) of the data series was performed using ASDHR40 and conducted within Matlab. The approach belongs to the Unobserved Components Modelling group of methods applying spectral decomposition to the observation series $${y}_{t}$$ isolating and estimating slow trends $${T}_{t}$$ as well as cyclic and seasonal components $${C}_{t}$$ and $${S}_{t}$$ respectively and the irregular component $${e}_{t}$$. This is executed using a stochastic state-space approach with Kalman Filtering and Fixed Interval Smoothing40 but placed within an irregular sampling framework. The arbitrary sampling, a novel approach in this context41, allows the Unobserved Components model to be estimated using irregularly sampled data.

$${y}_{t}={T}_{t}+{C}_{t}+{S}_{t}+{e}_{t}$$

In this case, no cyclic component was estimated and the seasonal component is expressed as:

$${S}_{t}=\sum _{i=1}^{{R}_{s}}\{{a}_{i,t}\,\cos ({\omega }_{i}t)+{b}_{i,t}\,\sin ({\omega }_{i}t)\}$$

where ai,t and bi,t are stochastic Time-Varying Parameters (TVP) and $${\omega }_{i}$$ are the fundamental and harmonic frequencies associated with seasonality in the series (i = 1, 2, , Rs). The covariance parameters of the KF/FIS estimators are defined by the time scale of the estimated processes.

## Data Availability

Data can be obtained by contacting the corresponding author.

Publisher’s note: Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.

## References

1. 1.

Ormerod, S. J. et al. Multiple stressors in freshwater ecosystems. Freshwater Biology 55, 1–4 (2010).

2. 2.

Hering, D. et al. Managing aquatic ecosystems and water resources under multiple stress—An introduction to the MARS project. Science of the total environment 503, 10–21 (2015).

3. 3.

Jackson, M. C. et al. Net effects of multiple stressors in freshwater ecosystems: a meta‐analysis. Global Change Biology 22(1), 180–189 (2016).

4. 4.

Benda, L. et al. The network dynamics hypothesis: how channel networks structure riverine habitats. AIBS Bulletin 54(5), 413–427 (2004).

5. 5.

Lowe, W. H. & Likens, G. E. Moving headwater streams to the head of the class. AIBS Bulletin 55(3), 196–197 (2005).

6. 6.

Jones, J. B. & Stanley, E. Stream Ecosystems in a Changing Environment. Elsevier, London (2016).

7. 7.

Alexander, R. B. et al. The role of headwater streams in downstream water quality. JAWRA Journal of the American Water Resources Association 43(1), 41–59 (2007).

8. 8.

Wipfli, M. S., Richardson, J. S. & Naiman, R. J. Ecological linkages between headwaters and downstream ecosystems: Transport of organic matter, invertebrates, and wood down headwater channels. Journal of the American Water Resources Association 43(1), 72–85 (2007).

9. 9.

Kelly, M. & Whitton, B. A. The trophic diatom index: a new index for monitoring eutrophication in rivers. Journal of Applied Phycology 7(4), 433–444 (1995).

10. 10.

Kelly, M. et al. Assessment of ecological status in UK rivers using diatoms. Freshwater Biology 53(2), 403–422 (2008).

11. 11.

Stevenson, R., Pan, Y. & van Dam, H. Assessing environmental conditions in rivers and streams with diatoms. The Diatoms: Applications for the Environmental and Earth Sciences, 2nd ed. Cambridge University Press, Cambridge (2010).

12. 12.

European Commission. Directive 2000/60/EC of the European Parliament and of the Council of 23 October 2000 establishing a framework for community action in the field of water policy. Official Journal of the European Commission (2000). [cited 2018 22/03]; Available from: http://jncc.defra.gov.uk/.

13. 13.

Anonymous, Monitoring under the Water Framework Directive. Common Implementation Strategy for the Water Framework Directive Guidance Document No 7, 153 (2003).

14. 14.

Ockenden, M. et al. Changing climate and nutrient transfers: Evidence from high temporal resolution concentration-flow dynamics in headwater catchments. Science of the Total Environment 548, 325–339 (2016).

15. 15.

UKCP09. Climate change projections. 2014 [cited 2018 15/05]; Available from http://ukclimateprojections.metoffice.gov.uk/23189.

16. 16.

Rimet, F. & Bouchez, A. Life-forms, cell-sizes and ecological guilds of diatoms in European rivers. Knowledge and management of Aquatic Ecosystems 406, 01 (2012).

17. 17.

McCormick, P. V. Resource competition and species coexistence in freshwater benthic algal assemblages, in Algal ecology freshwater benthic ecosystems, R.J. Stevenson, Bothwell, M. L. and Lowe, R. L., Editor. Academic Press: London (1996).

18. 18.

Stelzer, R. S. & Lamberti, G. A. Effects of N: P ratio and total nutrient concentration on stream periphyton community structure, biomass, and elemental composition. Limnology and Oceanography 46(2), 356–367 (2001).

19. 19.

Gottschalk, S. & Kahlert, M. Shifts in taxonomical and guild composition of littoral diatom assemblages along environmental gradients. Hydrobiologia 694(1), 41–56 (2012).

20. 20.

Snell, M. A. Headwater Stream Biofilm Structure and Function at High Resolution Spatial-Temporal Scales, PhD, Lancaster University Lancaster. Lancaster (2014).

21. 21.

Soininen, J. & Eloranta, P. Seasonal persistence and stability of diatom communities in rivers: are there habitat specific differences? European Journal of Phycology 39(2), 153–160 (2004).

22. 22.

Wu, N. et al. Importance of sampling frequency when collecting diatoms. Scientific reports 6, 36950 (2016).

23. 23.

Lange, K. et al. Light, nutrients and grazing interact to determine stream diatom community composition and functional group structure. Freshwater Biology 56(2), 264–278 (2011).

24. 24.

Ockenden, M. C. et al. Major agricultural changes required to mitigate phosphorus losses under climate change. Nature Communications 1–9 (2017).

25. 25.

Woodward, G., Perkins, D. M. & Brown, L. E. Climate change and freshwater ecosystems: impacts across multiple levels of organization. Philosophical Transactions of the Royal Society B: Biological Sciences 365(1549), 2093–2106 (2010).

26. 26.

Segner, H., Schmitt-Jansen, M. & Sabater, S. Assessing the impact of multiple stressors on aquatic biota: the receptor’s side matters. Environmental Science and Technology 48(14), 7690–7696 (2014).

27. 27.

Pizarro, H. et al. Impact of multiple anthropogenic stressors on freshwater: how do glyphosate and the invasive mussel Limnoperna fortunei affect microbial communities and water quality? Ecotoxicology 25(1), 56–68 (2016).

28. 28.

Owen, G. J. et al. Monitoring agricultural diffuse pollution through a dense monitoring network in the River Eden Demonstration Test Catchment, Cumbria, UK. Area 44(4), 443–453 (2012).

29. 29.

WFD-UKTAG. River Assessment Method Macrophytes and Phytobenthos. Scotland. Water Framework Directive – United Kingdom Advisory Group (2014).

30. 30.

Krammer, K. & Lange-Bertalot, H. Süßwasserflora von Mitteleuropa, Bd 2/4. Bacillariophyceae. 4. Teil: Achnanthaceae Kritische Ergänzungen zu Navicula (Lineolatae) und Gomphonema. Gustav Fisher Verlag: Stuttgart (1991).

31. 31.

Krammer, K. & Lange-Bertalot, H. Susswasserflora von Mitteleuropa. Bacillariophyceae Teil iv: Achnanthaceae. Gustav Fischer Verlag: Stuttgart (1991).

32. 32.

Krammer, K. & Lange-Bertalot, H. Süßwasserflora von Mitteleuropa. Bacillariophyceae, Band 2/3, 3. Teil: Centrales, Fragillariaceae, Eunoticeae. 1-576. Gustav Fischer Verlag: Stuttgart (1991).

33. 33.

Krammer, K. & Lange-Bertalot, H. Süsswasserflora von Mitteleuropa. Bacillariophyceae. 1. Teil: Naviculaceae, vol 2/1. Gustav Fischer Verlag: Stuttgart (1986).

34. 34.

Kelly, M. Identification of common benthic diatoms in rivers. Field Studies Council 9, 583–700 (2000).

35. 35.

Hofmann, G., Werum, M. & Lange-Bertalot, H. Diatomeen im Süßwasser-Benthos von Mitteleuropa: Bestimmungsflora Kieselalgen für die ökologische Praxis; über 700 der häufigsten Arten und ihrer Ökologie. Gantner (2011).

36. 36.

Kelly, M. Building capacity for ecological assessment using diatoms in UK rivers. Journal of Ecology and Environment 36(1), 89–94 (2013).

37. 37.

Ewen, J. et al. Multiscale experimentation, monitoring and analysis of long-term land use changes and flood risk-SC060092: Final Science Report. Newcastle University, Newcastle upon Tyne, UK (2010).

38. 38.

Šmilauer, P. & Lepš, J. Multivariate analysis of ecological data using CANOCO 5. Cambridge University Press. United Kingdom (2014).

39. 39.

Braak, C. J. F. & Šmilauer, P. CANOCO reference manual and user’s guide: software for ordination (version 5.0). 2012: Biometris.

40. 40.

Young, P. C., Pedregal, D. J. & Tych, W. Dynamic harmonic regression. Journal of forecasting 18(6), 369–394 (1999).

41. 41.

Mindham, D. A., Tych, W. & Chappell, N. A. Extended State Dependent Parameter modelling with a Data-Based Mechanistic approach to nonlinear model structure identification. Environmental Modelling & Software 104, 81–93 (2018).

## Acknowledgements

We thank our funding project: Defra FFG0909 Design and implementation of monitoring approach at catchment scale, and development of the catchment conceptual (WQ0210). We would also like to thank other Eden Demonstration Test Catchment colleagues who have contributed to this research platform and the wider Demonstration Test Catchment team.

## Author information

M.A. Snell: Collection, processing and analyses of diatom samples with supporting environmental datasets available within the Eden Demonstration Test Catchment platform. Conceived concept for paper and wrote the manuscript with support from P.A. Barker. Discussed the results with all co-authors and edited the final manuscript. P.A. Barker: Contribution to the establishment, development and management of the Demonstration Test Catchment monitoring platform. Conceived concept for paper, contribution to formulation and writing of the manuscript. Discussed the results with M.A. Snell and contributed to editing of the final manuscript. Supervised the findings of this work. B.W.J. Surridge: Contributed to the design, implementation and supervision of diatom work and its findings. Contribution to the Eden Demonstration Test Catchment monitoring platform. Discussed the results and contributed to the final manuscript. C.McW.H. Benskin: Contribution to the collection of diatom and environmental datasets within the Eden Demonstration Test Catchment. Discussed the results and contributed to the editing of the final manuscript. N. Barber: Contribution to data collection and QC/QA analysis of environmental datasets within the Eden Demonstration Test Catchment. Discussed the results and contributed to the final manuscript. S.M. Reaney: Contribution to the establishment and development of the Eden Demonstration Test Catchment monitoring platform. Discussed the results and contributed to the final manuscript. W. Tych: Contribution to data analysis, specifically Arbitrary Sampled Dynamic Harmonic Regression modelling and discussed the results. Contributed to the final manuscript. D. Mindham: Contribution to data analysis, specifically Arbitrary Sampled Dynamic Harmonic Regression modelling and discussion of results. Contributed to the final manuscript via assistance with modelling graphics and editing. A.R.G. Large: Contributed to the design, implementation and supervision of diatom work and its findings. Discussed the results and contributed to the final manuscript and editorial. S. Burke: Contribution to the establishment and development of the Eden Demonstration Test Catchment monitoring platform. Discussed the results and contributed to the final manuscript. P.M. Haygarth: Contribution to the establishment, development and management of the Eden Demonstration Test Catchment monitoring platform. Discussed the results and overarching concept. Contributed to the final manuscript.

### Competing Interests

I declare that there are no financial or non-financial interests that could directly undermine, or be perceived to undermine the objectivity, integrity and value of this publication, through a potential influence on the judgements and actions of authors with regard to objective data presentation, analysis and interpretation.

Correspondence to M. A. Snell.