ALBERT

Notes: SUMMARY. Barton Broad, Norfolk is a shallow, eutrophic lake. During the last 30 years submerged macrophytes have declined and phytoplankton numbers have increased. This change is traced through the stratigraphy of a 60-cm mud core. Diatom frustule counts of 1-cm sections of the core showed that an epiphyte-dominated diatom community was replaced by a planktonic community. From chemical analysis and radio-isotope dating of the core, sedimentation rates and past phosphorus and iron loadings are estimated. Sedimentation rates were between 1.2 mm and 3.1 mm year−1 during the early part of the core but doubled in the 1950s to 5 mm year−1, doubled again in the 1960s and have increased to 12 mm year−1 in the 1970s. Retention of phosphorus in the sediment increased from 0.5 g m−2 year−1 to 18–21 g m−2 year−1 in two steps. A similar trend is shown for iron. The diatom species composition and chemistry of the core sections are correlated with increased nutrient loading and the decline of macrophytes. Contemporary phosphorus and iron budgets are calculated from inflow–outflow data and balanced using sediment retentions estimated from the core data. It is believed a large proportion of phosphorus and iron enters the Broad by movement of sediment along the river bed. A reduction of 25% of the 1975 phosphorus loadings would probably permit re-establishment of some macrophytes. The present chemistry and algal communities of Barton Broad and the River Ant are described.

Notes: 〈list xml:id="l1" style="custom"〉1 A review is presented of the literature on riparian vegetated buffer strips (VBS) for use in stream-water-quality restoration and limitations associated with their use are discussed. The results are also presented of recent investigations on the effectiveness of a forested and a grass vegetated buffer strip for reducing shallow subsurface inputs of nutrients from agriculture to a stream in central Illinois, U.S.A.2 Because riparian zones link the stream with its terrestrial catchment, they can modify, incorporate, dilute, or concentrate substances before they enter a lotic system. In small to mid-size streams forested riparian zones can moderate temperatures, reduce sediment inputs, provide important sources of organic matter, and stabilize stream banks.3 Several questions on the utility and efficiency of vegetated buffer strips for stream restoration still remain unanswered, including: what types (grass v forest) are most efficient; do they become nutrient saturated; are they only temporary sinks; how does species composition influence effectiveness; and, what is the optimal width of buffer to facilitate nutrient reduction under different conditions?4 Water samples were collected (1989–90) from lysimeters located at three depths (60, 120, and 〉 120cm) in an upland area planted in conventional row crops (corn and soybean) and in three adjacent riparian buffer treatments, a 39m wide grass buffer. a 16 m wide mature forested buffer, and a buffer planted in row-crops to the stream bank. Concentrations of dissolved and total phosphorus and nitrate-N in each sample were determined following major precipitation events over a seventeen month period.5 Both the forested and grass VBS reduced nitrate-N concentrations in shallow groundwater (up to 90% reduction). On an annual basis the forested VBS was more effective at reducing concentrations of nitrate-N than was the grass VBS, but was less efficient at retaining total and dissolved P.6 During the dormant season, both grass and forested buffer strips released dissolved and total P to the groundwater. The VBS apparently acted as a nutrient sink for much of the year, but also released accumulated nutrients during the remaining portion of the year. Periodic harvesting of plant biomass may reduce the amount of P released during the dormant season.7 VBSs are not as effective in agriculture areas with tile drained fields. Alternative restoration practices such as discharging drain tiles into wetlands constructed parallel to the stream channel may prove to be a more effective means of controlling non-point-source agricultural inputs of nutrients in such areas.

Notes: 〈list xml:id="l1" style="custom"〉1 An extreme drought in 1988 dried first- and second-order streams in the Salt Fork basin (1190 km2) in east-central Illinois. This event provided a natural experiment in which the natural rehabilitation of fish populations could be measured in the whole catchment following resumption of stream flows.2 Fish were sampled before, during, and after the drought (1987–1990) throughout the basin (eighty-eight samples in July-September) using methods of known efficiency. Analyses of covariance [using log (distance from source) as the covariate] indicated no significant differences (P〉0.2) of biomass or species richness between pre-drought and post-drought samples from sites desiccated during 1988 or among pre-drought, drought, and post-drought years among samples from perennial Streams. Therefore, recovery occurred within 1 year, but there was no indication of increased biomass or species richness in permanent streams resulting from fish moving down or remaining downstream during the drought.3 Fish biomass per unit length of stream segment was modelled as a power function of distance of the segment from the source of each stream to estimate changes in biomass of the whole catchment. Before and subsequent to the drought, 90.0t of fish occupied the total 729km of stream length in the basin, compared with 74.61 in the drought year. Although, the drought affected 80% of total stream length, fish biomass was reduced by only 17% in the drought year because only the lower-order streams were desiccated and their normal biomass density was lower than in perennial streams.4 In conclusion, it is expected that no expenditure on stocking fish would be necessary in restoration projects on these lower-order, surface runoff streams, providing that they are connected to permanently flowing streams that contain a full complement of species.

Notes: The River Slea through Sleaford is fed by groundwater emanating from the Lincolnshire Limestone. In recent years, the springs have dried up periodically, causing failure of river flow through the town. The Slea is a main feature of the town and, when flowing, a valuable visual amenity. Conversely, when it is not flowing, progressive water quality deterioration in ponded sections reduces the river corridor to an eyesore. The paper describes investigations into the cause of the problem and how to overcome it.